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Home > VOLUME 30 > ISSUE 3 > Article 34 Research

Remittance income weakens participation in community-based natural resource management

Benedum, M. E., N. J. Cook, and S. Vallury. 2025. Remittance income weakens participation in community-based natural resource management. Ecology and Society 30(3):34. https://doi.org/10.5751/ES-16436-300334
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  • Michelle E. BenedumORCID, Michelle E. Benedum
    Institute of Behavioral Science, University of Colorado at Boulder, USA
  • Nathan J. CookORCIDcontact author, Nathan J. Cook
    Paul H. O'Neill School of Public and Environmental Affairs, Indiana University Indianapolis, USA
  • Sechindra ValluryORCIDSechindra Vallury
    Odum School of Ecology, University of Georgia, USA

The following is the established format for referencing this article:

Benedum, M. E., N. J. Cook, and S. Vallury. 2025. Remittance income weakens participation in community-based natural resource management. Ecology and Society 30(3):34.

https://doi.org/10.5751/ES-16436-300334

  • Introduction
  • Research Context
  • Literature Review
  • Methods
  • Results
  • Discussion
  • Conclusion
  • Acknowledgments
  • Data Availability
  • Literature Cited
  • community-based natural resource management; forestry; migration; Nepal; participation; remittances
    Remittance income weakens participation in community-based natural resource management
    Copyright © by the author(s). Published here under license by The Resilience Alliance. This article is under a Creative Commons Attribution 4.0 International License. You may share and adapt the work provided the original author and source are credited, you indicate whether any changes were made, and you include a link to the license. ES-2025-16436.pdf
    Research

    ABSTRACT

    While many Global South contexts rely on community-based natural resource management, out-migration has the potential to change rural peoples’ incentives to participate in such management. We argue that remittance income from out-migration reduces dependence on natural resource commons, which may in turn weaken the voluntary participation upon which community-based natural resource management initiatives depend. We studied this relationship empirically in Nepal, a country with a largely community-based model for the governance of its forests. In analyzing nationwide survey data that spanned nearly one decade, we fit a household-level fixed-effects regression model, which showed that households that received more remittance income were less likely to rely on commonly held forests compared to households in the same village that received less remittance income. Using a similar estimation approach and more detailed survey data from the districts of Mustang and Gorkha, we also showed that larger remittance incomes predicted less participation in forest governance and management activities. These results suggest that the remittances associated with out-migration from rural areas can weaken incentives for local participation in natural resource management among the people left behind. If remittance income has these effects, policymakers may need to reconsider how to sustain community-based resource management in countries or regions that are experiencing widespread rural out-migration. Future research is needed to establish causality, validate the results cross-nationally, and explore new policy innovations that could support resource governance in contexts where many resource users receive remittances.

    INTRODUCTION

    The economic and environmental importance of common-pool resources in many Global South countries has motivated governments to adopt community-based natural resource management (CBNRM) programs, wherein rural people manage collectively owned natural resources through participatory processes (Cook et al. 2023, Cook 2024). These programs are designed to protect fragile environments, conserve ecosystem services, and support rural development. However, rural livelihoods remain highly vulnerable to environmental uncertainty and resource scarcity (Steffen et al. 2018), thus prompting many households to rely on out-migration as a livelihood adaptation strategy.

    CBNRM relies on voluntary participation, which makes it essential to understand the factors that influence engagement in these programs (Cook 2024). For example, in Nepal’s community forestry program, rural villagers engage in afforestation, forest monitoring, and rule enforcement to sustain local forests (Cook et al. 2023). Studies have highlighted the success of such initiatives in improving conservation outcomes (Oldekop et al. 2019), but those initiatives also play a crucial role in rural development. More than one billion people globally live in or near forests, and many depend on forest resources for daily subsistence and income (Newton et al. 2020). Community forestry can further benefit rural economies by generating revenue through the sale of forest products, which finances local public goods such as schools, roads, and other important infrastructure (Pokharel et al. 2007, Dongol et al. 2009, Ojha et al. 2009, Cook 2024).

    The degree to which households participate in CBNRM is shaped by economic incentives and livelihood strategies. In Nepal, participation in community forestry often involves membership in one of the approximately 22,000 community forest user groups, which collectively manage 35% of the country’s forests (Gentle et al. 2020, Cook et al. 2023, Cook 2024). Beyond membership, participation can entail taking on leadership roles, engaging in forest management activities, or having a voice in the decision-making processes (Molinas 1998, Agarwal 2001, 2016, Cook 2024). Many rural households depend on forests for firewood, fodder, and non-timber forest products (Angelsen et al. 2014, Cook 2024), which creates strong incentives for engagement in local governance. However, as households gain access to alternative income sources, such as remittances from migrating family members, those incentives may shift, raising concerns about declining participation in CBNRM.

    Out-migration has become increasingly common in rural areas, leading many households to transition away from subsistence-based economies toward remittance-dependent livelihoods. As rural households increasingly rely on remittances, global financial flows reflect this shift. In 2018, low- and middle-income countries received 529 billion U.S. dollars in remittances, a nearly 10% increase from the previous year (World Bank Group 2018). In some regions, migration has reduced reliance on local agriculture and common-pool resources because remittances provide an alternative source of income (Marquardt et al. 2016).

    Despite increasing attention to migration’s role in rural economies, little is known about how remittance income affects participation in community-based resource management. While research has linked out-migration to labor shortages that reduce participation in collective resource management (e.g., Bista et al. 2023), an alternative hypothesis suggests that remittance income may weaken household members’ incentives to engage in CBNRM institutions by reducing reliance on common-pool resources for both subsistence and small-scale commercial activities (Robson and Nayak 2010, Shrestha and Fisher 2017, Poudyal et al. 2023). However, few studies have systematically tested the effect of remittance income on participation in CBNRM across different localities, or estimated the magnitude of the relationship.

    We address this gap by using nationwide survey data from Nepal to examine the relationship between remittance income and two household outcomes: community forest use and participation in community forestry. We define out-migration as the relocation of one or more household members outside the village while the rest of the household remains in place, rather than full-household migration. This distinction is important in our study context, where partial household migration is the dominant pattern and it aligns with our theoretical framework, which emphasizes the role of remittance income in reshaping economic incentives for participation in CBNRM.

    By leveraging nationwide panel survey data that spanned nearly a decade, we systematically evaluate how remittance income influences household engagement in community forestry, and distinguish this effect from related factors such as labor shortages due to migration. While recent research has linked out-migration to labor shortages that reduce participation in collective resource management (e.g., Bista et al. 2023), an alternative possibility is that remittance income plays a more decisive role in reducing the use of community resources and participation in community resource management. Thus, we empirically test which mechanism has a stronger influence on participation in Nepal’s community forestry program. This distinction is crucial for policy design because it suggests that governments that are seeking to sustain participation in CBNRM models in high-migration environments may need to develop financial incentives or institutional adjustments that reflect evolving economic realities.

    A growing body of qualitative and case study research suggests that multiple factors, including remittance income, labor shortages, shifts in agrarian economies, and preferences for traditional resource management over government-led programs, may contribute to declining participation in community-based management (Poudel 2019, Poudyal et al. 2023). However, few studies have systematically examined the specific role of remittance income in shaping participation in CBNRM at a national scale or have sought to disentangle its effects from other migration-related factors. Our study fills that gap by providing empirical evidence on the relationship between remittances and participation in community forestry, and contributing to broader debates on migration, rural livelihoods, and common-pool resource governance.

    A theoretical model of the effects of out-migration and remittances on participation in community-based natural resource management, tested on empirical data from community forest systems, is important for policymaking and practice in the forestry sector. Since community engagement is fundamental to the sustainability of these governance models, socioeconomic changes that weaken participation in CBNRM programs may threaten their long-term viability. If remittance income reduces household members’ incentives to engage in collective governance, CBNRM institutions may face declining participation, which will require policymakers to consider adaptive strategies that sustain engagement amid economic and demographic shifts. Our study contributes to these discussions by testing a theoretical model of how out-migration and remittances affect participation in community-based resource management, using empirical data from Nepal’s community forestry system. Strengthening institutional support for rural communities that are experiencing these transitions will be essential to ensuring the resilience of community-based governance models.

    RESEARCH CONTEXT

    We use community forestry in Nepal as a test case through which to explore the relationships between remittance income, community forest use, and community forestry participation. In Nepal, the community forestry initiative has been implemented under the Forest Act of 1993 (Kanel and Kandel 2004). The Forest Act ordered the Department of Forests to establish community forest user groups in forested rural communities, starting in the 1990s (Ministry of Forests and Soil Conservation 2013, Cook et al. 2023, Cook 2024, Cook et al. 2025). As of 2020, there were more than 22,000 community forest user groups across Nepal (Gentle et al. 2020). These groups managed approximately 35% of Nepal’s forest resources, through the participation of approximately 3 million member-households (Gentle et al. 2020). Community forest user groups exist across the three ecological regions in Nepal—the northernmost Mountain Region of the Himalaya, the southern Terai Region that borders India, and the Middle Hill Region (Cook et al. 2023, Cook 2024).

    Previous research has described how community forestry is governed (Ojha et al. 2009, Cook et al. 2023, Cook 2024, Cook et al. 2025). Once a community forest user group is established, collective property rights over a plot of forested land are formally granted to the group. The community forest user group is charged with governing the communal use of forest products—mainly firewood, fodder, and other non-timber forest products—by its respective member-households. Since community forest user groups are largely self-governed, they are tasked with writing their own rules, establishing rationing systems and collecting royalties on allowable forest products, and engaging in monitoring, forest maintenance activities, and enforcement (Ojha et al. 2009,Cook et al. 2023, Cook 2024).

    As in many low- and middle-income countries, rural livelihoods in Nepal depend on natural resources, but they also depend on remittances from out-migration. In 2020, the country received 7.4 billion U.S. dollars in remittances, accounting for 23% of its GDP (World Bank Group 2020). Nearly 50% of households in Nepal have at least one member working abroad (International Organization for Migration 2019). Nepal is an ideal test case for understanding the relationship between migration, remittance income, and participation in community-based natural resource management. Not only is the community forestry program mature, large, and well-institutionalized, but widespread rural out-migration during our study period—coupled with the fact that forest dependence has historically been high in rural Nepal—makes the country a most likely case for detecting these relationships. Furthermore, recent scholarship argues that community forestry participation is likely declining in some parts of Nepal, and qualitative evidence suggests that this decline might be driven by out-migration and reduced reliance on forests, among other factors (Poudel 2019, Poudyal et al. 2023). Thus, we use nationwide survey data and econometric methods to examine the role that remittance income may be playing in this changing context.

    Our empirical analysis focuses on the study period of 2003–2012, due in part to the availability of large survey datasets from that period (see Methods). However, because our goal was to use Nepal as an empirical test case for exploring the general, theorized relationship between remittance income and community forestry engagement (established in Literature Review), this time period is particularly appropriate because there was a dramatic influx of remittance income as a percentage of GDP (World Bank Group 2025). Much of this was driven by out-migration from the types of rural communities that use community forest management models (Giri and Darnhofer 2010). Thus, although our data are from 2003–2012, we argue that Nepal during this study period provides a test case through which we may understand social processes that likely weaken participation in CBNRM in settings beyond Nepal that experience similar social and economic dynamics.

    LITERATURE REVIEW

    We explore the dynamics of rural out-migration and its implications through two key lenses. First, we review the current literature on “push” and “pull” factors in rural out-migration. This review spans the field of development studies, including development economics, to provide a comprehensive understanding of how scholars have studied the factors driving rural out-migration in the Global South context. Second, we review the relationship between rural out-migration and collective action in the context of common-pool resource management. This examination draws extensively on scholarship from the fields of common-pool resource governance and collective action, and offers insights into how rural out-migration influences and interacts with collective efforts to manage shared resources.

    Push and pull factors in rural out-migration

    Theory on rural out-migration has established that the motives for livelihood diversification through out-migration vary significantly across socioeconomic groups (Lambin et al. 2001, Zimmerer 2010). There is an important distinction between out-migration undertaken to manage risks and cope with environmental stressors on natural resources, characterized primarily by “push” factors, and out-migration undertaken for wealth accumulation, hence driven by “pull” factors (Reardon et al. 2007). The literature examined these push and pull factors by focusing on patterns of household adaptation through income diversification strategies in the Global South (García-Barrios et al. 2009, Hoffmann et al. 2019, Leblond 2019). While out-migration driven by push factors is usually associated with households’ adaptation to poverty and consumption and risk smoothing (de Janvry et al. 1991, Dressler et al. 2016), out-migration driven by pull factors is usually positively associated with an upward spiral of household wealth (Barrett et al. 2001a, Gray 2009).

    Rural households are pushed to out-migrate to cope with environmental risks, especially where missing insurance and credit markets often lead households to pursue different coping strategies against uncertainty in resource availability (Barrett et al. 2001b). Empirical evidence confirms that a key factor that pushes households to migrate and seek nonfarm livelihoods is a decline in seasonal income from farm-related activities (Abdulai and Delgado 1999). Therefore, remittances from seasonal out-migration allow these households to smooth their income inter-seasonally (Von Braun et al. 1990, Reardon et al. 2007). This type of out-migration is in fact not a means of coping with a shock, but is a planned, ex-ante adaptation to a long-term seasonal variation in resource availability and income. A second push factor for out-migration is a transitory decline in income due to an unexpected stressor (e.g., drought) that forces households to out-migrate as an ex-post adaptation strategy (Choithani et al. 2021). Out-migration is particularly prominent in rural communities where resource-based livelihoods constitute the dominant economic activity. This is because households depend more on remittances that are not subject to environmental risks that are covariant with those of the local agricultural economy (Poapongsakorn et al. 1998, Barrett and Swallow 2006).

    On the other hand, households in resource-rich areas are more likely to out-migrate to pursue attractive income diversification opportunities. For example, in the wetter and more stable agricultural zones of West Africa, households are more likely to out-migrate and diversify into nonfarm activities (Reardon et al. 1992, Haggblade et al. 2010). Indeed, empirical evidence shows that high-income households in buoyant rural economies are more likely to diversify into non-resource-based livelihoods (e.g., food processing and preparation, farm equipment repair, manufacturing) that have high returns because they have the necessary financial capital and skilled labor to pursue these profitable activities (Haggblade et al. 2010, Loison 2016). In such instances, there is evidence of a Markovian process whereby households invest remittances from out-migration into activities that enhance their resource productivity and/or human capital, such as technology upgradation, cash cropping, education, and further rounds of out-migration and income diversification (Estudillo and Otsuka 1999, Mohapatra et al. 2006, Robson and Berkes 2011, Hajjar et al. 2021).

    Linking rural out-migration and collective action

    Debates about how out-migration impacts collective management of natural resources have never been definitively settled, in part because there are multiple forms of migration in different resource contexts and participant groups (Connell and Conway 2000, Choithani 2017, Bhattarai 2020). We identify four key mechanisms through which out-migration may shape collective action in common-pool resource governance:

    • Labor constraints: Increased out-migration reduces labor availability for managing shared resources, which increases the costs of collective action (Cárdenas et al. 2017, Shin et al. 2022).
    • Resource dependence: Households that receive remittances may become less reliant on common-pool resources, which lowers their incentive to participate in community-based management (Wang et al. 2016).
    • Opportunity costs: Increased access to external incomes raises the opportunity costs of engaging in collective management, thus making participation less attractive (Rudel 2011, Sapkota et al. 2020).
    • Compensatory participation: In some cases, remaining household members (e.g., women) may step into leadership roles and contribute more to collective action efforts (Hecht et al. 2015, Leder et al. 2024).
    These mechanisms highlight the ambiguous relationship between out-migration and collective action, with some pathways reducing participation while others may sustain or even increase engagement. Furthermore, participation in collective action may have feedback effects on migration decisions: communities with well-functioning collective institutions may provide local economic opportunities that reduce the need for out-migration, while declining participation in resource management may degrade natural resources and further incentivize migration.

    To clarify these relationships, we present a conceptual figure on these mechanisms and feedback loops (Fig. 1). This figure provides a structured framework for interpreting how out-migration influences participation in CBNRM and how these relationships may reinforce or weaken each other over time.

    Participation in CBNRM is shaped in part by cost-benefit trade-offs. Households weigh the excludable benefits of participation, such as access to forest products and financial capital, against the costs, including time spent in meetings, resource maintenance, and opportunity costs (Ministry of Forests and Soil Conservation 2013, Bluffstone et al. 2020, Cook 2024). Remittances influence these trade-offs by reducing dependence on community-managed resources and making alternative income sources more viable (Shrestha and Fisher 2017, Fox 2018). Consequently, households that receive remittances may opt out of participating in CBNRM, thus increasing the marginal cost of management for poorer households that are reliant on those resources (Angelsen et al. 2014, Nguyen et al. 2015, Cook 2024).

    While the research identifies four key mechanisms through which out-migration may shape collective action, we focus on how remittance income influences two of them: household use of community forests, and participation in CBNRM activities. These theoretical propositions lead to the following two hypotheses:

    H1: Households that receive more remittances will be less likely to use collectively managed natural resources.

    H2: Households that receive more remittances will participate less in community-based natural resource management.

    METHODS

    To test our hypotheses, we used data from two sources: the Nepal Living Standards Survey (NLSS) and the Poverty Environment Network (PEN) survey initiative. The NLSS is a national-level, multi-topic household survey, collected during three periods: NLSS-I (1995–1996), NLSS-II (2003–2004), and NLSS-III (2010–2011) (Central Bureau of Statistics 1996, 2005, 2011a). The PEN initiative is a global comparative survey of households in 334 communities across 24 Global South countries (PEN 2016a). We used PEN data collected in Nepal, which provides socioeconomic, institutional, and environmental data at the household level from sampled locations in Mustang District and Gorkha District. We tested H1 by using data from the NLSS to fit a household-level model that predicted the collection of forest products from a local community forest as a function of the amount of remittance income received by the household, and we tested H2 by using the PEN data to fit a household-level model that predicted time allocation to community forest user group activities as a function of the amount of remittance income received. While previous analyses modeled forestry outcomes as a function of changes in migration at the aggregate level (Oldekop et al. 2018), our household-level analysis allowed us to measure household-level decisions, and to draw inferences about micro-level processes that link migration to community forest use and participation.

    Testing the relationship between remittances and community forest use

    The model used to test H1 was fit on an analytic sample of 3661 households in 338 rural communities, drawn from two distinct cross-sections from the 2003–2004 and 2010–2011 periods of the NLSS. Equation 1 represents this regression model:

    Equation 1 (1)

    The dependent variable (community forest use) is a dichotomous measure of whether the household reported collecting firewood or fodder from a community forest in the past 12 months, since these are two of the key products available to participants in community forestry (Agarwal 2010, Ministry of Forests and Soil Conservation 2013). Here, clogit represents the standard conditional fixed effects logistic regression model described in Chamberlain (1980), and π represents a vector of community-level conditional fixed effects. To measure remittance income, we used a variable (remittances) that represented the amount of remittance income the household received during the past year based on the household’s self-reported data. We converted these amounts to U.S. dollars using exchange rates from the year of each survey period (Central Intelligence Agency 2022) and converted them to their dollar equivalents in January 2022 (U.S. Bureau of Labor Statistics 2022). To facilitate interpretation, we rescaled this variable to be represented in hundreds of dollars. This variable includes both domestic and international remittances. While it is true that international migration tends to yield larger amounts of remittance income than does domestic migration in our study context, our theoretical model suggested that receiving a given amount of remittance income will shift the perceived costs and benefits of participating in community forestry similarly, regardless of whether the source is international or domestic. Thus, we used absolute amounts of remittance income from all sources as our independent variable of interest.

    We controlled for several household-level covariates. First, we controlled for whether the household belonged to the ethnic or caste group that was most numerous in the community (ethnic majority). Because ethnicity is assigned at birth, this variable is exogenous to migration and the receipt of remittances. Previous studies have found ethnicity and caste to be highly related to community forestry participation rates and the distribution of benefits from community forestry, which makes this an important covariate to control for (Agarwal 2016, Cook 2024). We also included a dichotomous educational attainment variable (education) that measured whether the oldest living male household member received any formal schooling. We added this control because educational attainment is a widely recognized proxy for a household’s economic background and has significant implications for economic behavior and decision-making processes (Duflo 2001). Additionally, we controlled for household size (measured as the number of individuals living in the household). Controlling for household size is important because it affects the distribution of resources within the household and the overall economic burden. Larger households might have different consumption needs and income-generating capacities compared to smaller ones (Lanjouw and Ravallion 1995).

    Finally, we controlled for three additional income sources: respondent households’ net income from crop sales (crop income), the sale of animal products (animal income), and enterprises owned by household members (enterprise income). We measured these three covariates in the NLSS data using households’ reported gross income from each activity type during the year preceding the survey, minus their reported expenditures for inputs related to each activity type during the same period. Like the remittance income variable, we converted these values to January 2022 U.S. dollars and scaled them so they were expressed in hundreds of dollars. Including these income sources allowed us to account for variations in household economic activities and their impact on overall income, thereby addressing potential biases from unobserved heterogeneity (Morduch 1995, Dercon 2002). While our list of controls did not capture every possible household characteristic, they were chosen based on their relevance to our research questions and their empirical support in existing literature. Our approach balanced the need for parsimony in model specification with the inclusion of key variables that were critical for our analysis.

    We calculated nonparametric bootstrap-clustered standard errors using the cluster resampling method recommended by Cameron et al. (2008) to correct the confidence intervals and P values reported for our logistic regression model. In line with this method, communities were resampled with replacement, coefficient estimates were calculated for each replication, and standard errors were calculated from the resultant distribution using the procedure provided in Cameron et al. (2008:416).

    This modeling approach predicted the relative odds of a household’s community forest use as a function of the amount of remittance income received by that household, while holding the household-level control variables constant. Additionally, community fixed effects held community characteristics constant in the model. Because our analytic sample from the NLSS was from two distinct, cross-sectional samples of communities across the two periods included in our study, the community fixed effects were equivalent to community–year fixed effects, and therefore also controlled for potential confounding differences between the two time periods that may have influenced the estimates. This analysis of the NLSS microdata thus allowed us to estimate the relationship between remittance income and community forest use at the level of the individual household while controlling for household characteristics, community fixed effects, and time effects. However, because remittance income was not assigned at random to households, there is still the possibility of omitted household-level variables that may have biased the estimated relationship between remittance income and community forest use. We therefore cannot assume that the causal effect of remittance income on community forest use was necessarily identified in our model, and we treat our analysis as correlational. In Appendix 1, we replicated the results while controlling for additional household characteristics.

    Testing the relationship between remittances and participation

    To explore the relationship between remittance income and participation in community forest user groups, we used the Nepal subsample of the PEN data. Our analytic sample consisted of 453 households across five communities in Mustang District and two communities in Gorkha District, surveyed in 2005–2008. While the PEN survey protocol involved interviewing households at multiple different time points, each household was asked about community forest user group participation during only one of those interviews. Our sample is therefore cross-sectional. In the villages surveyed, households in Mustang were asked about their participation in 2005. In Gorkha, households were asked about their participation in 2008.

    To estimate the association between remittances and participation in community forestry, we used a zero-inflated negative binomial regression model. It was estimated in two stages, represented by Equation 2 and Equation 3:

    Equation 2 (1)

    Equation 3 (1)

    The first stage of this model (Eq. 2) predicted the logged odds of whether or not the respondent household reported zero days of participation in community forest user group activities over the past 12 months (nonparticipation). Then, for the subset of respondent households that reported a non-zero number of days spent participating, the second stage (Eq. 3) predicted their degree of participation, measured by the number of person-days that household members reportedly spent on community forest user group activities over the past 12 months (days). One person-day was equivalent to one full working day for a single household member (see PEN 2016b). Here, logit refers to the standard logistic regression model, NBin refers to a negative binomial regression model, and σ is a dispersion parameter.

    To measure remittances in the PEN data, we used the same technique as for the NLSS data. The independent variable used in this model represented the total annual amount of remittances received by the household from individuals living outside the village during the survey year, expressed in hundreds of dollars. In both stages, the zero-inflated negative binomial regression model included the same household-level controls as described previously. δ and λ represent vectors of unconditional community-level fixed effects included in the first and second stages of the model, respectively. Because the analytic dataset was cross-sectional, the community fixed effects were equivalent to community–year fixed effects, and thus controlled for differences between communities as well as potentially confounding temporal differences between the 2005 time period (when the Mustang households were surveyed) and 2008 (when the Gorkha households were surveyed). Although there were seasonality differences between the Mustang and Gorkha households, with the former surveyed in December and the latter surveyed in March, our community-level fixed-effects controlled for seasonality differences since the season in which households were surveyed varied across communities but not between them; thus, the community-level fixed-effects addressed the effects of seasonality. We corrected the reported confidence intervals and P values for community-level clustering by calculating cluster-robust standard errors using the sandwich estimator described by Rogers (1993).

    As before, this analysis controlled for key characteristics of households, as well as community fixed effects, but we could not rule out the possibility of unmeasured confounding variables at the household level in this correlational analysis. However, in Appendix 1, we replicated the results of this analysis while controlling for additional household characteristics.

    Characteristics of samples

    Table 1 shows summary statistics for each analytic dataset, and Fig. 2 maps the locations of surveyed households at the district level. Our analytic sample from the NLSS spanned all three ecological regions of the country—the northernmost Mountain Region, the Terai Region that borders India, and the Middle Hill Region, which lies between. Furthermore, rural households from almost every district were included in the sample. By contrast, our analytic sample from the PEN survey covered the districts of Gorkha and Mustang. Thus, while the Middle Hill Region and Mountain Region were reflected in our test of H2, the Terai Region was not because it was not covered by the PEN survey. Readers should note this limitation. While our test of the relationship between remittance income and community forest use was based on a large analytic sample with substantial geographic and temporal coverage, our test of the relationship between remittances and community forestry participation was somewhat more limited, and it is possible that the results of our test of H2 do not generalize to the Terai Region.

    Although the PEN sample did not cover the Terai region, the trends in our variables of interest were largely similar across both datasets. As shown in Table 1, the NLSS and PEN samples exhibited similar trends in household income portfolios, education, ethnic majority status, and household size. Both samples showed substantial average remittance incomes ($98 for the NLSS sample and $535 for the PEN sample). On average, households earned more from enterprise income ($321 for the NLSS sample and $104 for the PEN sample) than from livestock, and the average household in both samples experienced net negative crop incomes (-$43 for the NLSS sample and -$48 for the PEN sample). More than 50% of households in the NLSS sample and nearly 42% in the PEN sample had formal education. More than 50% of households in the NLSS sample and more than 60% in the PEN sample belonged to the local ethnic majority. The average household size was 5.2 persons for the NLSS sample and 6.2 persons for the PEN sample.

    RESULTS

    Remittance-receiving households are less likely to use community forest resources

    Table 2 shows the conditional logistic regression results from the household-level model fit on the NLSS data. Estimate (a) shows the estimated relationship between a household’s remittance income and their relative odds of collecting forest products from a community forest. This estimate suggests that remittances have a negative and statistically significant association with the likelihood of collecting products from a community forest (P < 0.006). We calculated the average magnitude of this association on the probability scale using the average semi-elasticity method (Kitazawa 2012). On average, an increase in remittance income of one standard deviation predicted a roughly -8% change in the probability of reporting community forest use (95% CI: -14%, -2%). While the purpose of our model was to estimate the relationship between remittances and community forest use while controlling for the covariates, some readers may also find it worth noting that household size was the only covariate with a statistically significant test statistic (in the positive direction). Estimates on the ethnic majority and education variables exhibited wide confidence intervals.

    Remittance-receiving households spend less time on community forestry participation

    Table 3 shows the results from the zero-inflated negative binomial regression model fit on the PEN survey data. Estimate (c) in Table 3 represents the estimated relationship between a household’s remittance income and the number of person-days spent by household members on community forest user group activities (expressed as an incidence-rate ratio), and estimate (b) represents the relationship between remittance income and the odds of a household reporting participation at all. Estimate (c) indicates that remittances had a statistically significant negative association with the number of person-days spent on community forestry activities among households that reported participating.

    These model results are easiest to interpret through model predictions expressed as the raw number of predicted person-days that households spent on community forestry activities (Fig. 3). These predictions suggest that on average, households that did not receive remittances spent just over four person-days per year on community forestry activities. In contrast, households that reported receiving US$2500 per year in remittances (a difference of roughly two standard deviations, relative to households that did not receive remittances) were predicted to spend three person-days per year on community forestry activities, or nearly 25% less time relative to households that did not receive remittances. In our PEN survey sample, 13% of remittance-receiving households reported receiving this amount or more.

    In addition to the statistically significant relationship between remittance income and community forestry participation, three covariates had statistically significant test statistics in the first stage of the zero-inflated negative binomial regression, with negative signs: household size, education, and ethnic majority. Confidence intervals for other covariate coefficient estimates were generally wide.

    Data limitations and alternative specifications

    Our econometric models controlled for a range of covariates that could confound the relationship between remittance income, community forest use, and community forestry participation. In addition to the observable household-level characteristics discussed in the Methods, fixed effects controlled for unobservable and observable confounding variables at the community–year level. Nonetheless, it was not possible to rule out all potential confounding variables in this observational study, particularly if they operated at the household level (rather than the community level or community–year level). For example, the 2003–2004 period of the NLSS coincided with a Maoist insurgency that occurred across rural Nepal, and some evidence suggests that local exposure to the conflict impacted the governance of community forest user groups (Nightingale and Sharma 2014). Local conflict intensity, if it is indeed a confounding variable, is most likely to be a community-level confounding variable rather than a household-level confounding variable; therefore, it is less likely that our results were confounded by local exposure to the conflict once community-level fixed effects were controlled for. Nonetheless, if household-level conflict exposure was correlated with households’ remittance income and with their decisions to use community forests or participate in community forestry for enough households in our samples (after controlling for community–year fixed effects and our other covariates), then the variable would cause household-level confounding that we would be unable to control for.

    Thus, since our analysis was based only on observable household-level covariates, it is possible that certain omitted household-level social or economic characteristics influenced our results. For example, gender, caste, and ethnicity are likely correlated with remittance income and are known to influence decisions about community forestry participation and benefits from community forestry (Agarwal 2016, Cook et al. 2023, Shrestha et al. 2023, Cook 2024). Furthermore, the number of remittance-senders, not remittance income, may reduce the likelihood that a household will use collectively managed natural resources. All of these covariates are measurable in the NLSS data, and gender is measurable in the PEN data, whereas the other covariates are not (in both datasets, gender is operationalized through the gender of the household head). In Appendix 1, we replicated our results while controlling for these characteristics; our results were stable when these additional covariates were included in our models.

    Because we cannot completely rule out the possibility of unobservable household-level confounding variables in our study, future studies should use more robust, quasi-experimental research designs to further explore the relationships between out-migration, remittance income, and the use and governance of collectively managed natural resources.

    DISCUSSION

    Empirical insights

    We provide quantitative evidence that out-migration, via remittance income, influences both the use of shared natural resources and participation in CBNRM. Our findings from the forestry sector in Nepal support two key mechanisms. First, households that receive remittances are less likely to depend on products from community forests. As rural livelihoods shift from resource-based activities to urban employment and service-sector jobs (Jaquet et al. 2019), reliance on shared natural resources diminishes. This reduced dependence weakens households’ incentives to participate in collective management.

    Second, and relatedly, remittance income is associated with lower levels of participation in CBNRM activities. While research has suggested that multiple factors, such as out-migration-related labor shortages, socioeconomic transformations, and resistance to government schemes, influence participation in CBNRM (Poudel 2019, Shahi et al. 2022, Poudyal et al. 2023), our study isolates the effect of remittance income, which is distinct from the number of out-migrants. These findings contrast with those of Bista et al. (2023), who hypothesized a link between community forestry participation and remittance income but found no significant statistical evidence. Our zero-inflated negative binomial regression model suggests that while remittance income does not reduce the probability of participation, it significantly reduces the amount of time households allocate to community forestry activities. This may be because households that receive remittances maintain superficial ties to community-based institutions, such as occasionally attending community forest user group meetings, while drastically reducing their engagement in actual forest management activities. This would align with previous qualitative research that has shown that in some communities where participation has dwindled, members or even community forestry leaders maintain nominal ties to community institutions but contribute little time to resource management (Poudyal et al. 2023). The moderate magnitude of the estimate indicates that in settings where many households receive a large amount of annual remittance income, as is the case for some households that receive remittances from international locations (Central Bureau of Statistics 2011b), we would expect to see a noticeable reduction in the amount of time and effort allocated to community forestry. The estimate does not, however, suggest that there are substantial changes in participation by households that receive only a modest amount of such income (as is common for some other households, particularly those that receive remittances from domestic locations).

    It is also notable that these relationships hold when controlling for the number of out-migrants, and the number of out-migrants has no apparent relationship with our forestry-sector outcome variables, while controlling for the amount of remittances received (see Appendix 1). This is in contrast to some other empirical work that has shown that decisions to implement many other conservation activities in the agricultural sector show the opposite pattern: they appear to be influenced by the number of out-migrants and not the amount of remittances received (Williams and Paudel 2020). This highlights the importance of developing sector-specific models for understanding the social and economic dimensions of conservation decision-making, rather than assuming that those social and economic dimensions are the same across sectors.

    CONCLUSION

    Implications for policy and future research

    Although our study was based in Nepal, the findings have broader relevance for community-based resource management programs globally. The effectiveness of CBNRM depends on sustained participation for monitoring, enforcement, ecosystem restoration, and rural development. If participation declines due to socioeconomic shifts linked to out-migration, policymakers may need to reconsider how to sustain collective governance structures.

    One potential response is to develop targeted programs that strengthen incentives for participation among households that receive remittances. Research suggests that women left behind by out-migration face participation constraints shaped by caste and social networks (Shrestha et al. 2023). To address these challenges, pro-poor entrepreneurship strategies in community-based resource management (Paudel 2012) could help marginalized households derive economic benefits from forestry. Effective implementation would require partnerships with government and non-governmental organizations (Cronkleton et al. 2012), which could help to ensure that such initiatives do not erode local participation but instead foster sustainable engagement. Such partnerships could help develop effective donor programs with local user buy-in by encompassing tasks such as identifying poor and marginalized households, devising production and benefit-sharing plans, implementing monitoring and evaluation procedures, and establishing conflict resolution mechanisms regarding resource use. These efforts could ultimately build the resilience of community-based natural resource systems (Nightingale and Sharma 2014). Therefore, future policy development should focus on creating an enabling an environment for commercial livelihoods in the context of community-based programs (Sapkota et al. 2020).

    Our findings also raise important questions for future research. While we documented participation shifts due to remittance incomes, further studies should examine the long-term impacts on the sustainability of CBNRM institutions. Specifically, how do declining participation rates influence afforestation efforts and resource management outcomes? Additionally, exploring whether participation patterns differ across social groups, such as wealthier versus marginalized households, would provide insights into equity concerns in CBNRM governance (Sunam and McCarthy 2016, de Brauw 2019). If wealthier households withdraw from collective management, this may leave marginalized groups with disproportionate responsibility for maintaining community forests, which would reinforce existing socioeconomic inequalities (McCarthy et al. 2009, Maharajan et al. 2012, Dustmann and Okatenko 2014, Cook 2024).

    Finally, while our study identified correlations between out-migration, remittance incomes, and participation in CBNRM, future research should employ causal identification strategies to strengthen policy recommendations. The findings also open avenues for cross-national comparisons using similar datasets, such as those developed through the cross-national PEN survey initiative. Expanding this research across different regions would help determine whether the observed patterns in Nepal apply to other community-based governance systems that are experiencing high out-migration. Similarly, there is room for future work to investigate whether our results from the 2003–2012 period fully capture present-day dynamics in Nepal. Although this study period is useful for studying the general relationship between remittance incomes and community forestry, and yields lessons that are relevant to countries that are currently experiencing out-migration from community forest systems, it is possible that some of these dynamics have either changed or intensified in Nepal since the time of data collection. We note this limitation so as to discourage readers from misinterpreting our results, and to encourage future data collection to study the dynamics of migration and forestry in Nepal.

    Our study underscores the complex relationship between out-migration, remittance income, and community-based resource management. As rural economies transition due to migration, natural resource governance institutions must adapt to shifting participation dynamics. Understanding these evolving relationships is critical for ensuring the long-term sustainability of CBNRM models, particularly in regions where migration-driven socioeconomic transformations are accelerating.

    RESPONSES TO THIS ARTICLE

    Responses to this article are invited. If accepted for publication, your response will be hyperlinked to the article. To submit a response, follow this link. To read responses already accepted, follow this link.

    ACKNOWLEDGMENTS

    This research was supported by the National Science Foundation (grants: #1757136, #2242507, #2343136). We thank the Central Bureau of Statistics in Kathmandu and the Poverty Environment Network (PEN) program for providing the data used in this study. We thank Dr. Krister Andersson and Dr. Ganesh Gorti for their constructive comments and suggestions about this work.

    Use of Artificial Intelligence (AI) and AI-assisted Tools

    AI-assisted tools were not used in the research and writing process.

    DATA AVAILABILITY

    The National Living Standards Survey data analyzed in this study were provided by the Central Bureau of Statistics of the Government of Nepal. A data use agreement prohibits the authors from sharing these data. However, the datasets generated and analyzed during the current study are available from the corresponding author on reasonable request if prior permission is granted from the original data providers (where applicable).

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    World Bank Group. 2020. Migration and development. Brief 33. World Bank, Washington, D.C., USA.

    World Bank Group. 2025. Personal remittances, received (% of GDP) – Nepal. https://data.worldbank.org/indicator/BX.TRF.PWKR.DT.GD.ZS

    Zimmerer, K. S. 2010. Biological diversity in agriculture and global change. Annual Review of Environment and Resources 35:137-166. https://doi.org/10.1146/annurev-environ-040309-113840

    Corresponding author:
    Nathan Cook
    cooknath@iu.edu
    Appendix 1
    Fig. 1
    Fig. 1. Out-migration influences participation in community-based natural resource management (CBNRM) through four potential mechanisms: labor constraints, resource dependence, opportunity costs, and compensatory participation. Arrows with plus (+) signs denote reinforcing effects (an increase in one variable leads to an increase in the connected variable); minus (-) signs indicate balancing effects (an increase in one variable leads to a decrease in the connected variable).

    Fig. 1. Out-migration influences participation in community-based natural resource management (CBNRM) through four potential mechanisms: labor constraints, resource dependence, opportunity costs, and compensatory participation. Arrows with plus (+) signs denote reinforcing effects (an increase in one variable leads to an increase in the connected variable); minus (-) signs indicate balancing effects (an increase in one variable leads to a decrease in the connected variable).

    Fig. 1
    Fig. 2
    Fig. 2. Study setting. Colors indicate the number of households surveyed in a given district across the Nepal Living Standards Survey (NLSS) sample (left) and Poverty Environment Network (PEN) sample (right).

    Fig. 2. Study setting. Colors indicate the number of households surveyed in a given district across the Nepal Living Standards Survey (NLSS) sample (left) and Poverty Environment Network (PEN) sample (right).

    Fig. 2
    Fig. 3
    Fig. 3. Association of remittances and the number of days spent on community forestry activities. Predictions were based on the results of a zero-inflated negative binomial regression model (see <em>Methods</em> and Table 3). As the amount of remittance income increased, the predicted number of person-days spent on community forestry activities decreased (CFUG: community forest user group).

    Fig. 3. Association of remittances and the number of days spent on community forestry activities. Predictions were based on the results of a zero-inflated negative binomial regression model (see Methods and Table 3). As the amount of remittance income increased, the predicted number of person-days spent on community forestry activities decreased (CFUG: community forest user group).

    Fig. 3
    Table 1
    Table 1. Descriptive statistics for household survey samples.

    Table 1. Descriptive statistics for household survey samples.

    Mean Median SD Min Max
    Nepal Living Standards Survey sample (N = 3661)
     Dependent variable
      Community forest use 0.437 0 0.496 0 1
     Independent variable
      Remittance income (100 U.S. dollars) 0.978 0 4.831 0 122.974
     Control variables
      Crop income (100 U.S. dollars) -0.429 -0.149 7.568 -72.263 397.798
      Animal income (100 U.S. dollars) 0.261 0 2.6021 -16.082 39.619
      Enterprise income (100 U.S. dollars) 3.209 0 14.879 -135.272 501.729
      Education 0.544 1 0.498 0 1
      Ethnic majority 0.503 1 0.500 0 1
      Household size 5.205 5 2.305 1 26
    Poverty Environment Network sample (N = 453)
     Dependent variable
      Participation (days) 4.159 3 4.919 0 30
     Independent variable
      Remittance income (100 U.S. dollars) 5.348 0 11.077 0 124.521
     Control variables
      Crop income (100 U.S. dollars) -0.483 -0.408 1.343 -7.271 8.757
      Animal income (100 U.S. dollars) 0.005 0 2.454 -21.942 14.038
      Enterprise income (100 U.S. dollars) 1.043 0 4.075 -3.184 39.351
      Education 0.419 1 0.494 0 1
      Ethnic majority 0.678 1 0.468 0 1
      Household size 6.192 6 2.591 1 18
    Table 2
    Table 2. Association of remittances and the use of community forest resources. Odds ratios were estimated using logistic regression with conditional fixed effects at the community level. The dependent variable was a dichotomous indicator of whether or not the household collected firewood or fodder from a community forest over the past 12 months. 95% confidence intervals were calculated using cluster-bootstrapping at the community level. <em>N</em> = 3661.

    Table 2. Association of remittances and the use of community forest resources. Odds ratios were estimated using logistic regression with conditional fixed effects at the community level. The dependent variable was a dichotomous indicator of whether or not the household collected firewood or fodder from a community forest over the past 12 months. 95% confidence intervals were calculated using cluster-bootstrapping at the community level. N = 3661.

    Variable 95% confidence interval P
    Independent variable
     (a) Remittances (100 U.S. dollars) 0.970 [0.950, 0.991] 0.006
    Control variables
     Ethnic majority 0.900 [0.738, 1.097] 0.299
     Education 0.954 [0.795, 1.145] 0.612
     Household size 1.071 [1.028, 1.117] 0.001
     Crop income 1.012 [0.992, 1.033] 0.246
     Animal income 1.002 [0.965, 1.040] 0.920
     Enterprise income 0.994 [0.986, 1.003] 0.190
    Conditional fixed effects (community level) X
    Table 3
    Table 3. Association of remittances and the number of person-days spent on community forestry activities. Exponentiated coefficients were estimated with a zero-inflated negative binomial regression model. The dependent variable was the number of person-days a household reported spending on community forestry activities in the previous 12 months. The first stage predicted the likelihood of a household reporting zero days of participation in community forestry activities. For households with non-zero community forestry participation, the second stage predicted the number of person-days spent on community forestry activities. The model included unconditional fixed effects at the community level. <em>N</em> = 453. 95% confidence intervals were corrected for clustering at the community level.

    Table 3. Association of remittances and the number of person-days spent on community forestry activities. Exponentiated coefficients were estimated with a zero-inflated negative binomial regression model. The dependent variable was the number of person-days a household reported spending on community forestry activities in the previous 12 months. The first stage predicted the likelihood of a household reporting zero days of participation in community forestry activities. For households with non-zero community forestry participation, the second stage predicted the number of person-days spent on community forestry activities. The model included unconditional fixed effects at the community level. N = 453. 95% confidence intervals were corrected for clustering at the community level.

    First stage: Odds of zero participation in community forestry activities (logistic; odds ratios) Second stage: Number of person-days spent on community forestry activities (negative binomial; incidence-rate ratios)
    Independent variable
    Remittances (100 U.S. dollars) (b) 1.011 (c) 0.992
    [0.985, 1.037] [0.987, 0.997]
    P = 0.401 P = 0.001
    Control variables
    Ethnic majority 0.244 1.334
    [0.142, 0.421] [0.945, 1.885]
    P = 0.003 P = 0.102
    Education 0.230 1.134
    [0.162, 0.328] [0.969, 1.327]
    P < 0.001 P = 0.117
    Household size 0.900 0.998
    [0.871, 0.929] [0.969, 1.028]
    P < 0.001 P = 0.909
    Crop income -0.052 0.962
    [0.575, 1.566] [0.878 - 1.055]
    P = 0.838 P = 0.411
    Animal income 1.104 0.991
    [1.005, 1.212] [0.951 - 1.034]
    P = 0.038 P = 0.684
    Enterprise income 0.973 0.997
    [0.890, 1.063] [0.975 - 1.020]
    P = 0.543 P = 0.815
    Constant 10.830 3.595
    [5.859, 20.02] [2.949 - 4.381]
    P < 0.001 P < 0.001
    Fixed effects (community level) X X
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    Home > VOLUME 30 > ISSUE 3 > Article 33 Research

    Downstream impacts of the Madeira Hydroelectric Complex on várzea traditional agriculture and extractivism

    Lobo, G. S., J. O. Gil, R. F. B. da Silva,‬ and E. F. Moran. 2025. Downstream impacts of the Madeira Hydroelectric Complex on várzea traditional agriculture and extractivism. Ecology and Society 30(3):33. https://doi.org/10.5751/ES-16518-300333
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    • Guilherme S. LoboORCIDcontact author, Guilherme S. Lobo
      Programa de Pós-Graduação em Ambiente e Sociedade do Instituto de Filosofia e Ciências Humanas (IFCH), UNICAMP, Brazil; Núcleo de Estudos e Pesquisas Ambientais (NEPAM), UNICAMP, Brazil
    • Jorge O. Gil, Jorge O. Gil
      Institute of Agro-Environmental Research and Sustainable Organizations (IEPAGRO), Porto Velho, Rondônia, Brazil
    • Ramon F. B. da Silva‬ORCID, Ramon F. B. da Silva‬
      Núcleo de Estudos e Pesquisas Ambientais (NEPAM), UNICAMP, Brazil
    • Emilio F. MoranORCIDEmilio F. Moran
      Michigan State University, USA

    The following is the established format for referencing this article:

    Lobo, G. S., J. O. Gil, R. F. B. da Silva,‬ and E. F. Moran. 2025. Downstream impacts of the Madeira Hydroelectric Complex on várzea traditional agriculture and extractivism. Ecology and Society 30(3):33.

    https://doi.org/10.5751/ES-16518-300333

  • Introduction
  • Methods
  • Results
  • Discussion
  • Conclusion
  • Responses to this Article
  • Author Contributions
  • Acknowledgments
  • Use of Artificial Intelligence (AI) and AI-assisted Tools
  • Data Availability
  • Literature Cited
  • Amazon; extractivism; flood recession agriculture; hydropeaking; traditional livelihoods
    Downstream impacts of the Madeira Hydroelectric Complex on várzea traditional agriculture and extractivism
    Copyright © by the author(s). Published here under license by The Resilience Alliance. This article is under a Creative Commons Attribution 4.0 International License. You may share and adapt the work provided the original author and source are credited, you indicate whether any changes were made, and you include a link to the license. ES-2025-16518.pdf
    Research

    ABSTRACT

    Hydropower development in the Amazon has accelerated under public and private incentives, aiming to promote economic growth, environmental conservation, renewable energy, and social equity within a sustainable development agenda. However, recent studies show significant negative impacts on local communities and ecosystems, raising concerns about hydropower’s true contribution to sustainability. Despite increasing awareness, research has largely overlooked the downstream effects of hydropower dams. Since the Madeira Hydroelectric Complex became operational, it has introduced sub-daily flow oscillations (hydropeaking) in the Madeira River, Southwest Amazon. Although poorly understood, hydropeaking can disrupt the river’s essential flood pulse, which rural riverine communities, known as ribeirinho, depend on for traditional flood recession agriculture and extractivism in the whitewater floodplains (várzea). These communities have long adapted their livelihoods to seasonal flood dynamics, using both low- and high-gradient várzea floodplains, but this downstream flow alteration may be affecting the várzea social-ecological system and must be investigated. To investigate hydropeaking’s effects, we conducted semi-structured interviews with local experts (n = 51) of four downstream ribeirinho communities, along with hydrological and soil analyses. Our findings reveal a shift in agricultural practices, particularly in flood recession agriculture in low-várzea areas. Soil analysis corroborates local experts’ concern about declining fertility, showing reduced phosphorus content following dam operations. Additionally, the extreme 2014 flood and expanding illegal gold mining have further diminished engagement in extractivist activities. A truly sustainable future for the Madeira River depends on revitalizing várzea-based value chains while preserving both ecological integrity and social resilience. We recommend establishing an independent monitoring group composed of ribeirinho communities and local scientists to assess downstream impacts on the várzea social-ecological system. Furthermore, targeted compensation and mitigation projects should be implemented to promote the sustainable use of várzea resources.

    INTRODUCTION

    Hydropower is Brazil’s primary renewable energy source, accounting currently for about 60% of the electrical mix (Energy Research Office (EPE) 2024). Since the 1980s, hydropower development has been boosted, particularly in the Amazon basin, as it possesses immense hydraulic potential (von Sperling 2012). Hydropower development has been accelerated by government and private sector incentives aimed at fostering economic growth, environmental conservation, and social equity under a sustainable development agenda (Fearnside 2015, Moran and Athayde 2019). However, recent years have seen a proliferation of studies highlighting the adverse impacts of hydropower development on local communities’ well-being and the ecosystems of the Amazon (Athayde et al. 2019). This has led to growing concerns regarding the role of hydropower in sustainable development in the Amazon (Moran et al. 2018).

    Despite this increased awareness, certain types of impacts have received more attention than others. Major research efforts have concentrated on the direct impacts of the large dam construction and surrounding reservoir areas (Dias et al. 2018), including involuntary population resettlement and the repercussions of a large reservoir in ecological processes (Kirchherr et al. 2016, Cernea and Maldonado 2018). However, less scientific attention has been directed toward the downstream socio-ecological impacts of hydropower dams (Richter et al. 2010), especially within tropical regions (Winemiller et al. 2016, Runde et al. 2020). This constitutes a significant knowledge gap, given that the dam operation typically results in hydrological alteration downstream, often crossing jurisdictional boundaries over long distances (Nilsson et al. 2005, Poff and Schmidt 2016). Lost in hydropower development’s shadow, the downstream impacts have been overlooked in the Amazon, leading to recurrently underestimated and undercompensated impacts on people and the environment (Mayer et al. 2022c, García et al. 2024, Utsunomiya et al. 2024).

    In the Amazon, downstream dam regulation is a significant concern due to the intrinsic connection between aquatic ecosystems and the seasonal flow regime, described by Junk et al. (1989) as the flood pulse. The largest Amazonian rivers are characterized by a predictable monomodal flood pulse driven by dry and rainy seasons in their catchment basins (Junk et al. 2014). Along the margins of these rivers occur floodplains, which are crucial habitats for endemic and endangered species adapted to flood pulse (Junk and da Silva 1997, Wittmann et al. 2013). The flood pulse also regulates biochemical cycles within the floodplain (Melack 2016), such as soil and water nutrients (Melack and Forsberg 2001).

    Beyond its influence on biota and ecological processes, the flood pulse profoundly defines the livelihoods of rural traditional riverine communities (known as ribeirinho in Portuguese), who reside in floodplain areas, especially the biodiverse whitewater floodplain, locally known as várzea. The bond between traditional ribeirinho’s livelihoods, várzea, and flood pulse is so profound that it resonates in their identity, resource utilization, movements, and social activities (Harris 1998). For instance, ribeirinho communities manage agriculture and extractivism in the várzea in synchrony with flood pulse (Junk et al. 2020). In this sense, natural and human elements of the várzea are interrelated and inextricably shaped by the flood pulse, functioning as a complex socio-ecological system (Kumar et al. 2023).

    In this intertwined socioecological system, downstream dam regulation needs to be seen as an essential factor that pushes into a transitional state, eventually leading to new dynamic equilibria (Berkes and Folke 1998). Different components of the system that depend on the flood pulse adjust to flow regulation at varying rates. For instance, invertebrates and floodplain herbaceous vegetation may reach a new equilibrium within a few years (Baladrón et al. 2023), whereas fish and vegetation composition may continue adjusting for decades (Gandini et al. 2014, Bejarano et al. 2018). As the ecology adapts to the regulated flow, local residents, particularly farmers and extractivists, also adjust their livelihoods, which rely on floodplain resources (Thomas and Adams 1999). These adaptations are further influenced by broader economic and social factors from outside the floodplain, although their impacts are felt locally. However, few studies have explored how social-ecological systems adapt to downstream changes caused by dams, especially in the Amazon.

    Under this scenario lies the enormous Madeira Hydroelectric Complex (MHC), which has been damming the Madeira River, a large whitewater tributary of the Amazon River. Operation of the MHC causes a sub-daily flow oscillation (hydropeaking) due to the intermittent operation of floodgates associated with energy demand (Almeida et al. 2020). Despite being considered a minor variation in hourly flow, hydropeaking may have significant implications for the social-ecological dynamics, however, there have been no studies to date that investigated how ribeirinho communities perceive hydropeaking concerning the impacts and adaptation on the várzea agriculture and extractivism activities (Bipa et al. 2024, Jardim and Collischonn 2024). We hypothesize that even subtle fluctuations in water levels can disrupt várzea traditional livelihoods, influencing agriculture and extractivism practices, and broader ecological interactions.

    To test this hypothesis, we applied an interdisciplinary approach that combined interviews with 51 local experts from four downstream ribeirinho communities, daily and hourly hydrological analyses, and an assessment of soil chemical properties before and after the implementation of the MHC. A key aspect of our study was capturing the lived experiences of these communities, highlighting how hydropeaking influences their agricultural and extractivist activities within the várzea, a phenomenon largely understudied worldwide (Richter et al. 2010).

    METHODS

    Study site

    The Madeira River basin spans over 1.4 million km², encompassing parts of Bolivia, Brazil, and Peru. Formed by the confluence of the main tributaries of the Amazonian–Andean region (Beni, Mamoré, and Madre de Dios Rivers), it is recognized as one of the most significant whitewater rivers in the Amazon basin in terms of sediment load (Latrubesse 2008). Naturally, the Madeira River has a flood regime that varies about 10 m between the dry and rainy seasons (Junk et al. 2014). Along the Madeira River occurs the várzea, the most biodiverse floodplains (Wittmann et al. 2013), which are divided into low and high topographic gradients according to both scientific and local knowledge (Junk et al. 2012, Souza et al. 2012). The low-várzea is flooded annually for more than 3 mos. and covered by mud bars, grassland, or sparse forest vegetation, whereas the high-várzea is elevated, covered with dense forest vegetation, agroforestry systems, and flooded for less than 3 mos. during the highest peak.

    Within the várzea, several ribeirinho communities live and maintain their unique traditional livelihoods intricately tied to the flood regime rhythm (Harris 1998). They depend on the naturally fertile várzea soils for flood recessional agriculture, cultivating short-term crops (less than 90 d to produce), like beans (Vigna unguiculata), manioc (Manihot esculenta), and watermelon (Citrullus lanatus) in the low-várzea, especially in river mud bars. In the high-várzea, they practice conventional agriculture, planting long-term crops, such as corn (Zea mays), squash (Cucurbita sp.), and banana (Musa sp.). Also, they manage the high-várzea by adopting an agroforestry system to harvest essential forest resources, especially açaí (Euterpe precatoria) and other native fruits (Souza et al. 2012) (Fig. 1).

    Since 2013, the MHC, comprising the Jirau and Santo Antônio dams, has been fully operational on the Madeira River. The cascade operation of these two large run-of-river dams has triggered multiple hydrosedimentological changes, making the Madeira River the most environmentally vulnerable basin in the Amazon (Latrubesse et al. 2017). Located approximately 100 km apart, the combined effects of the dams affected downstream flood regime with significant increases in daily and sub-daily flow peaks (i.e., hydropeaking) (Almeida et al. 2020), significantly threatening the natural ecosystem state (Siddiqui et al. 2021). Additionally, the damming of the MHC has led to a decline in downstream sediment load (Li et al. 2020). Despite the ribeirinho communities’ fundamental connection to the várzea, they have had limited participation in environmental assessment reports of the MHC (Mayer et al. 2022a), leading to lack of compensation for losses in livelihoods and health (Mayer et al., 2022b, 2022c, García et al. 2024).

    Shortly after the completion of the MHC, an extreme flood event occurred in 2014. Driven by intense regional rainfall and aggravated by dam operations, the Madeira River reached unprecedented levels (Oliveira et al. 2021). This event resulted in irreparable losses for urban and rural populations along the Madeira River (Novoa Garzon and Silva 2020), and caused severe impacts on the várzea’s fauna and flora (Moser et al. 2019, Bobrowiec et al. 2021, Medeiros et al. 2023, Dayrell et al. 2024). This event exemplifies how the flood regime is the fundamental process governing the várzea, where the fates of people and nature are governed by the river’s rhythm (Jackson et al. 2022).

    Hydrological data collection and analysis

    Hydrological analyses were conducted using daily flow data (m³ s⁻) from the Madeira River, from 1967 to 2022, to identify hydropeaking events and assess other hydrological anomalies. The data were obtained from the Brazilian National Water Agency (Agência Nacional de Águas e Saneamento Básico (ANA)) database including two of the region’s most established and consistent downstream river gauges: the Porto Velho gauge (Code 15400000), located 5 km downstream of the Santo Antônio Dam, and the Humaitá gauge (Code 15300000), approximately 250 km downstream from the same dam. To evaluate hourly flood pulse oscillations, the analysis was restricted to years and river gauges with adequate data coverage (greater than 90% of the year with hourly data) during the MHC’s operation period (2013–2019). Hourly data for the pre-dam period were unavailable, and the Humaitá gauge has a large data gap for all time series, therefore, it was no longer considered. The comparison focused on the Porto Velho gauge, representing the impacted downstream area, and the Abunã gauge (Code 15320002), located 5 km upstream of Jirau dam and not impacted (Fig. 2).

    The daily flow data of the Madeira River was analyzed using the Indicators of Hydrologic Alteration (IHA) software, version 7.1, developed by the Nature Conservancy (2009). These analyses followed the IHA environmental flow protocol to evaluate the hydrological impacts of anthropogenic activities, focusing on key parameters related to hydropeaking. Daily rise and fall rates (m³ s⁻¹ h⁻¹) and the number of reversals were computed for periods before and after the construction of the MHC. Rise rates were determined by the median of positive differences between consecutive daily flow values, whereas the median of negative differences determined fall rates. Additionally, the number of reversals, defined as abrupt changes from rising to falling flow trends, was calculated for each seasonal flood pulse regime (October to September).

    Changes in the seasonal flood pulse of the Madeira River were further assessed by comparing monthly Pardé coefficients for periods before (1967–2012) and after (2013–2022) the construction of the MHC. The Pardé coefficient, the ratio of mean monthly discharge to mean annual discharge, indicates shifts in the seasonal flood pulse regime (Almeida et al. 2020).

    Sub-daily flood pulse oscillations were evaluated using the HP1 indicator (m³ s⁻¹ h⁻¹), which quantifies the magnitude of hydropeaking. This indicator is calculated as the difference between sub-daily maximum and minimum hourly flows, normalized by the mean daily flow (Carolli et al. 2015). The non-parametric Wilcox test was employed to assess the statistical significance using R software.

    Soil data collection and analysis

    The soil’s chemical properties were assessed by analyzing samples collected before and after the construction of the MHC. For the pre-construction period, we used data from the “Studies and Perspectives of Development for Downstream Madeira River 2010–2011” program (Souza et al. 2012). This program was conducted in collaboration with the Institute for Agri-Environmental Studies and Research and Sustainable Organizations (IEPAGRO) and the Santo Antônio Energia, the company responsible for the Santo Antônio Dam operation. The IEPAGRO program collected eight samples in productive areas of the low and high várzea of each downstream ribeirinho community expected to be impacted by dam regulation. The soil was sampled at 20 cm depth, during September and October 2011, which coincides with the Madeira River low water season. All samples were georeferenced and stored in geodatabases. The samples were analyzed for various soil chemical parameters, including base saturation (Al+H), calcium, magnesium, organic matter, pH, phosphorus, and potassium, following the Brazilian Agricultural Research Corporation (Embrapa) standardized protocol (Embrapa 1997).

    For the post-construction period, samples were collected during the low water season as well, in September and October 2023, adopting the same protocols used in 2011 and in the same georeferenced points. These samples were analyzed for the same soil chemical parameters following Embrapa standardized protocols (Embrapa 1997). The differences between soil chemical properties in the surveyed várzea were compared using the Student’s t-test, performed with the Python library scipy.stats.

    Interview data collection and analysis

    The interviews were conducted in four downstream non-indigenous rural riverine (ribeirinho) communities outside protected areas in Porto Velho, Rondônia State, Brazil: Cujubim Grande, São Carlos, Nazaré, and Calama (Fig. 2), which have a combined total population of 2,743 residents (Instituto Brasileiro de Geografia e Estatística (IBGE) 2024). From September 2022 to November 2023, we identified interviewees using a non-probabilistic “snowball” sampling method, an appropriate method for research with remote and dispersed groups (Russell 2005). The participants selected were local experts, defined for this study as community members recognized by their peers for their long-term practical knowledge of várzea agriculture and extractivism. A key inclusion criterion was at least 10 yrs of continuous residence downstream, including the period prior to the construction of the MHC.

    Semi-structured interviews were conducted with these selected participants to explore their perceptions of várzea agricultural and extractivism practices in the context of hydropeaking. Participants were asked about their agricultural and extractivism practices in both low-várzea and high-várzea. For extractivism, they were questioned about resource use, such as edible fruits, medicinal products, oils, palm hearts, resins, tannins, textile fibers, and timber.

    The interviews further explored any abnormal changes in the Madeira River’s daily flooding, and how these changes may have impacted their agricultural and extractivism activities over the past decade. Participants were asked to suggest and discuss possible causes when changes were noted.

    Interviews were conducted using the ArcGIS Survey123 on tablets, with audio recording, and took place in the participants’ homes or work environments. Before the interviews, participants were informed about the study’s objectives and provided consent, ensuring anonymity and the option to withdraw at any time. This study was approved by the Human Research Ethics Committee at the University of Campinas (CEP authorization number: 61440222.9.0000.8142).

    Interviews were transcribed to be analyzed in the Python “pandas” and “spacy” libraries. We implemented a content analysis approach to identify the most frequently mentioned terms across all interviews, focusing on the perceptions of local experts from ribeirinho communities regarding hydropeaking occurrence and the adaptation strategies in agriculture and extractivism within the várzea.

    RESULTS

    Hydrological data

    The mean monthly Pardé coefficient comparison between pre-dam and post-dam periods shows that Madeira River still preserves a seasonal flood pulse regime, validated with Porto Velho and Humaitá gauges flow data (Fig. 3).

    The flow rise rate (m³ s⁻¹ day⁻¹) showed a marked difference between the pre-dam (1967–2012) and post-dam (2013–2022) periods. Both river gauges recorded a significant increase in the rise rate following the dam’s operation (Porto Velho gauge, p < 0.001; Humaitá gauge, p < 0.05). Daily flow analysis revealed a 21.4% increase at the Porto Velho gauge and a 26.9% increase at the Humaitá gauge (Fig. 4a). The flow fall rate (m³ s⁻¹ day⁻¹) showed a significant increase of 33.1% at the Porto Velho gauge between the pre-dam and post-dam periods (p < 0.001). At the Humaitá gauge, there was a 6.2% increase in the fall rate, but it was not statistically significant (Fig. 4b). Daily flow analyses showed a 35.6% increase in flow reversals. The comparison between pre-dam and post-dam impact showed a 35.6% increase in the number of flow reversals at Porto Velho Station (p < 0.001). The Humaitá gauge showed a 5% increase in reversals (Fig. 4c).

    The comparison between Abunã and Porto Velho gauges hourly flow shows a significant downstream sub-daily flood pulse oscillation (p < 0.001), as the hydropeaking indicator (HP1) has a greater mean and standard deviation in the impacted region (Fig. 5).

    Soil data

    The soil chemical comparison between 2011 and 2023 from Cujubim Grande, São Carlos, Nazaré, and Calama revealed slight acidification and a general decline in fertility, with reductions in calcium, magnesium, phosphorus, and potassium levels. Despite these trends, only the decrease in phosphorus was statistically significant (p < 0.018), observed only in the low-várzea soils across all communities. Other parameters, such as base saturation (Al+H) and organic matter, showed less pronounced variations (Table 1).

    Survey data

    Agriculture and extractivism in the várzea

    A total of 51 local experts from four downstream ribeirinho communities were interviewed, one adult (over 18 yrs old) per family unit. Of these, 85% were male, with an average age of 58, and most had completed primary education. The interviews revealed that the importance of the várzea to local livelihoods has persisted after the establishment of the MHC. Ninety-six percent of respondents considered the várzea very important for their traditional livelihood. Local experts stated that low-várzea, especially river mud bars, are very important for the flood recessional agriculture of beans, manioc, and watermelon. The high-várzea are mostly used to plant bananas and sometimes squash, and harvest açaí, as exemplified by a ribeirinho from the Nazaré community:

    We plant beans and manioc on the river’s mud bars, and we grow long-term crops on the higher ground in the várzea. We plant bananas on the higher ground, and we also grow squash and harvest native açaí.

    For our purposes, respondents were asked if they perceived hydropeaking in the Madeira River in recent years. Eighty-five percent perceived hydropeaking. Among the respondents who perceived hydropeaking, the majority pointed to the MHC as the driver of this phenomenon (77.8%), 2.75% indicated illegal mining, 2.75% climate change, and 16.7% don’t know the reason. Regarding the predictability of the Madeira River flood rhythm, 89% of respondents stated that hydropeaking jeopardizes their capacity to predict daily flood levels. A ribeirinho from the São Carlos community who has been living in the region for 40 yrs reported that several bioindicators have changed with the hydropeaking, such as the inhambu bird (Crypturellus sp.) and river dolphin (Sotalia fluviatilis) behavior that used to be a signal of rising river water:

    The river is not normal. In the morning, it’s full, but by the afternoon, it dries up. We know that when the inhambu bird starts calling at night, the river will rise. We also know that when the dolphins start moving too fast, the river will rise. It used to be like that, but now it’s all messed up. The river can rise a meter from six in the evening until dawn. Then, during the day, it can drop by a meter and a half. We’ve lost our ability to predict the river.

    Seventy-five percent of respondents indicated that hydropeaking negatively impacts their agricultural practices. The most frequent agricultural activities in várzea cited by respondents that decreased after hydropeaking occurrence were beans (14), manioc (9), and watermelon (12), all mostly located in the low-várzea. This, in turn, led to the interruption of flood recessional agricultural practices that was described by a ribeirinho from Cujubim Grande:

    Nowadays, you can’t plant crops along the river’s mud bars like you used to. It’s too risky. You plant beans or anything else today, and by tomorrow it’s all flooded.

    Several respondents mentioned adapting their agricultural effort from the low-várzea to higher ground to avoid hydropeaking, frequently noting (16 mentions) increased banana production in high-várzea. Another issue created by the hydropeaking that motivated the focus in agriculture on high-várzea, is a misinterpretation of the natural reversal of the river flow, an abrupt change from rising to falling flow trends locally known as repiquete, which serves as an environmental signal of the beginning of the flooding season. According to a ribeirinho from the Calama community, the similarity of hydropeaking with repiquete confuses them:

    Before these dams, we were familiar with the signs of the flood and drought seasons. In October, we knew the first repiquete would come, with the water rising once and then receding. In early November, there would be a second repiquete. From late November to December, it would rain, and the water would start rising steadily. But it’s different now, it’s out of season. When it’s not expected, the water rises a little and then dries up, because they’re releasing water from the dams. It’s not affecting the high-várzea, but we used to plant on the river’s very productive mud bars. Now, we have to plant higher up.

    The ribeirinho local experts were asked if they perceived any change in the várzea soil fertility since the beginning of hydropeaking occurrences. Sixty-six percent of the respondents noted a decrease in soil fertility, 28% indicated no change, and 6% responded that they didn’t know. The deterioration of soil fertility was noted by a ribeirinho from the São Carlos community:

    The river is shallower now, depending on the outflow from the dams. The dams traps mud, so it no longer settles on the bars, making them more sandy. There’s only sand on the banks now, and the soil is weaker for cropping.

    According to the interviews, extractivism was not significantly impacted by hydropeaking, with açaí harvesting being cited three times as impacted, and araça-boi (Eugenia stipitata), bacaba (Oenocarpus bacaba), and cacao (Theobroma cacao) each cited only once. Aside from hydropeaking, several respondents declared that the extreme 2014 flood was a major event that caused disinterest in extractivism due to huge losses (being cited by 28 respondents), including displacing residents and diminishing açaí palms, as stated by another ribeirinho from São Carlos community:

    Here in São Carlos, a lot of people left because of the 2014 flood. The only ones who stayed were those who were pioneers here. I lost everything during the 2014 flood—my house and my crops, including around 1,500 açaí plants.

    During fieldwork, numerous illegal rafts and dredges extracting gold from the riverbed and banks were commonly observed. Despite the risks associated with this illegal activity, many ribeirinho community residents have shifted their labor efforts away from várzea recession agriculture and extractivism to gold dredging, transforming the agricultural landscape documented by IEPAGRO in 2011 to a marked mining-induced erosion in 2023 (Fig. 6a, b). Although interviewees acknowledged that gold dredging is illegal, some stated that it is the only economic alternative for them and their family members who live downstream from the MHC. As described by a ribeirinho from the Nazaré community:

    I’m not against ending illegal mining, but it needs to be done differently. We need to bring everyone together and provide economic alternatives that were lost after the dams. I’m tired of seeing the news frame us as criminals, when for us, this is the only way to sustain our families’ livelihoods.

    DISCUSSION

    We found that local experts from the four surveyed ribeirinho communities perceive the occurrence of hydropeaking, which aligns with data analysis from river gauges, demonstrating agreement between information sources. They recognize the specific impacts of hydropeaking, differentiating its effects on their traditional várzea flood recessional agriculture and extractivism based on topographic gradients. The low-várzea gradient was identified as being more severely impacted, particularly affecting the flood recessional cultivation of beans, manioc, and watermelon on the river’s mud bars. Additionally, ribeirinho local experts reported challenges in practicing agriculture in the low-várzea due to poor soil fertility, which was corroborated by soil analysis showing deficient phosphorus content. According to local experts, they have shifted their agricultural practices to the high-várzea gradient, away from the direct impacts of hydropeaking. However, this agricultural adaptation has not been reflected in extractivism. The interviewed local experts reported a decline in várzea extractivist activities, primarily due to consequences of the extreme 2014 flood event, which caused significant socio-ecological losses for communities along the Madeira River, as well as the emergence of alternative economic opportunities, such as gold mining.

    Our extended hydrological analysis corroborates the findings of Almeida et al. (2020), demonstrating that the operation of the MHC has significantly increased short-term flood pulse oscillations (hydropeaking). This impact is most pronounced near the complex, with attenuation observed further downstream, likely due to the influence of the channel, floodplain, and tributaries such as the Jamari and Ji-Paraná Rivers (Greimel et al. 2018). Despite this attenuation, distant downstream communities, such as Nazaré and Calama, still perceive hydropeaking as a disruptive force in their traditional livelihoods. Hydropeaking has also altered other aspects of local livelihoods. As highlighted by Santos et al. 2020, fishers in Humaitá, a city located 250 km downstream, reported declines in productivity due to the unpredictable flood pulse post-damming. Although hydropeaking is a subtler phenomenon compared with the impact of older Amazonian dams (Schöngart et al. 2021), it significantly alters how Amazonian traditional livelihoods interact with floodplains and rivers, as observed in this case and others, such as the Arara people from the Xingu River (Utsunomiya et al. 2024). Therefore, hydropeaking must be addressed by decision makers as a direct impact of the MHC that requires appropriate compensation.

    We found a new aspect of hydropeaking’s impact on traditional ribeirinho’s livelihoods according to local experts. Undoubtedly, the main hydropeaking impact perceived by local experts is predicting flood timing to practice flood recessional agriculture in the low-várzea. As noted by previous studies, flood recessional agriculture is risky when the flood regime becomes unpredictable (Coomes et al. 2016). For instance, early floods, similar to hydropeaking, cause substantial agricultural losses in the Peruvian Amazon (Langill and Abizaid 2020). In the case of the Madeira River, the persistent hydropeaking led to a significant decline in the efforts of local communities to develop flood recessional agriculture, dropping the traditional production of beans and manioc in river mud bars, both of which are rooted in ancient indigenous heritage (Watling et al. 2018). This disruption has driven ribeirinho community members to adapt, particularly anchoring their production effort in banana monoculture in the high-várzea areas. Such a focus on higher ground could potentially trigger a forest transition process in the high-várzea and upland areas due to limited access to flood recessional agriculture areas (Coomes et al. 2022).

    This study presents the first soil chemical assessment of agricultural várzea areas following the damming of the Madeira River, revealing a decline in soil phosphorus content in the low-várzea, consistent with local experts’ perceptions. The observed reduction in phosphorus in low-várzea soils is validated by water data (Almeida et al. 2015). Finer and Jenkins (2012) have raised concerns about the impact of damming the Madeira River on sediment load, as sediment trapping is a documented phenomenon in reservoirs worldwide (Dethier et al. 2022). Phosphorus depletion poses a significant threat to the entire social-ecological system, as phosphorus is a critical limiting macronutrient in the Amazon (Malhi et al. 2021). For instance, high productivity of várzea flood recessional agriculture is naturally sustained by nutrient-rich sediments deposited by the Madeira River, originating from the Andes (McClain and Naiman 2008). Therefore, declining phosphorus in the low-várzea soil is another key driver for the agricultural shift to higher ground, as local experts confirmed. In the case of várzea agriculture, phosphorus content depletion is especially concerning given the local logistical challenges of supplying phosphorus from outside the natural cycle (Morello et al. 2018). Moreover, phosphorus fertilization has been shown to increase phytoplankton biomass and productivity in central Amazon whitewater lakes and várzea (Melack and Forsberg 2001). In this sense, the decline in phosphorus may also be contributing to decreasing commercial fish yields in the Madeira River (Santos et al. 2018), as many fish species consumed in the Amazon rely on food chains that begin with phytoplankton (Forsberg et al. 1993).

    Surprisingly, extractivism was not frequently mentioned by interviewees as important to their livelihood, despite its potential to create sustainable chains for native products (Abramovay et al. 2021). A significant factor contributing to the disinterest in várzea extractivism was the substantial losses experienced during the extreme 2014 flood, which destroyed productive areas and residences (Novoa Garzon 2019). This event killed numerous várzea tree and herbaceous species (Oliveira et al. 2021, Medeiros et al. 2023), thereby likely reducing the availability of extractive resources (Evangelista-Vale et al. 2021).

    The decline in interest in agroextractivist practices in the várzea has been further exacerbated by the gold mining boom along the Madeira River. In recent years, many ribeirinho community members whose livelihoods were based on agriculture, extractivism, fishing, and hunting have turned to illegally extracting gold to increase their profits (Pestana et al. 2022). Despite mining being a fundamental economic activity in the Madeira River (Martins et al. 2022), it threatens local resilience due to its numerous impacts on the ecosystem and social structure of the traditional communities (Froese et al. 2022). With limited sustainable economic alternatives available, they are increasingly being pushed toward illicit activities that compromise the integrity of the regional social-ecological system (Marcovitch and Val 2024). Addressing this challenge requires urgent efforts to develop viable, sustainable livelihood options that align with the ecological and cultural realities of the region (Zerbini et al. 2024). Without such conservation interventions, the cycle of environmental degradation and social-economic vulnerability will only deepen, further endangering both the biodiversity and the ribeirinho well-being.

    CONCLUSION

    Our research explored the perceptions of local experts from ribeirinho communities regarding the downstream impacts caused by the MHC, combined with hydrological and edaphic data. Taking advantage of an interdisciplinary approach, our findings show that local experts have not only perceived these impacts but have also adapted their agricultural and extractivist practices within the várzea. To our knowledge, we provided the first evidence that the damming of the Madeira River is altering the phosphorus content of low-várzea soils. Although our study, based on a comparison of two periods, has limitations in confirming continuous soil chemical changes, it strongly indicates the need for continued monitoring of várzea soils and associated social-ecological impacts.

    Over the past decade, the downstream changes caused by the MHC have eroded existing resource base and traditional practices in the várzea. Without innovation or adequate support, agriculture has become limited to the high-várzea areas. At same time, low-várzea exhibited the higher downstream impact, diminishing flood recessional agriculture due to hydropeaking impact and phosphorus soil loss. Additionally, the extreme 2014 flood, in addition to “gold fever”, put pressure on people to find some other means of labor and subsistence, decreasing interest in várzea extractivism and agriculture.

    Although the findings from our 51 local experts’ interviews cannot be statistically generalized to the entire downstream population of Porto Velho, they are critically important, as these ribeirinho community members have experience with várzea agriculture and extractivism both before and after the operation of the MHC. Moreover, local knowledge of experts reflects deep social-ecological links that are often invisible to the general population (Wantzen 2024), being of great value to downstream dam assessment, as some impact can be perceived only by those who observe nature processes intimately and daily (Baird et al. 2021). For generations, ribeirinho communities have relied on várzea agriculture, extractivism, and fishing as their main economic activities. However, recent years have been particularly challenging, pushing them to limited viable economic alternatives. In this context, documenting local expert perceptions alongside empirical assessments, such as soil and hydrological analyses, is essential to capture the downstream impacts of large dams on these often-overlooked communities. This is particularly relevant for run-of-river dams, frequently promoted as sustainable energy solutions with minimal downstream consequences.

    Despite the conventional assumption that run-of-river dams cause only subtle flow variations, our findings demonstrate that hydropeaking promotes profound social-ecological consequences on the várzea system of the Madeira River. Given these impacts, it is imperative to involve ribeirinho communities in conservation initiatives and research efforts, ensuring close monitoring of downstream effects. The active participation of local communities in impact monitoring has proven successful in the case of the Belo Monte Dam, one of the most controversial hydropower projects in the Amazon, and aligns with conditions observed in the Madeira River. Along the Xingu River, ribeirinho communities and indigenous people have collaborated with local researchers to independently assess Belo Monte’s downstream effects, providing a counterpoint to the periodic social-environmental assessments conducted by the energy company, showing an often underestimated extent of social-ecological consequences (Quaresma et al. 2025).

    Similarly, in the Madeira River, the companies responsible for the hydroelectric complex, Jirau Energia and Santo Antônio Energia, have conducted hydrobiochemical monitoring in the downstream region. However, their assessments have consistently overlooked the downstream impacts on the várzea social-ecological system. In this context, our findings strongly recommend that ribeirinho communities of the Madeira River adopt an independent monitoring protocol inspired by the Xingu River experience. To implement such a monitoring system, we propose establishing partnerships with research institutions (e.g., Federal University of Rondônia - UNIR, and the National Institute for Amazonian Research - INPA), agroextractivist cooperatives, and local NGOs. Through these collaborations, ribeirinho residents could be trained by scientists to apply diverse monitoring methods that integrate local knowledge with scientific knowledge. The downstream region of the MHC is a particularly suitable setting for this collaborative monitoring system, as it could be built based on previous initiatives, such as the ForestFisher project, which supported participatory monitoring of artisanal fishing (Biodiversa+ 2024).

    Decision makers must recognize the unique vulnerabilities of ribeirinho communities living downstream of the Madeira Hydroelectric Complex and implement mitigation actions that restore hydrological conditions as closely as possible to natural flow patterns. Access to water is a fundamental right, not a commodity, and downstream communities must have real-time access to river flow information to adapt their livelihoods accordingly. A truly sustainable future for the Madeira River depends on revitalizing várzea-based value chains, preserving both ecological integrity and social resilience while preventing harmful activities such as illegal mining. In this sense, the sustainability of the Madeira River’s várzea social-ecological system requires integrating scientific assessments with local knowledge, prioritizing community-led solutions.

    RESPONSES TO THIS ARTICLE

    Responses to this article are invited. If accepted for publication, your response will be hyperlinked to the article. To submit a response, follow this link. To read responses already accepted, follow this link.

    AUTHOR CONTRIBUTIONS

    Conceptualization: GSL, RB, and EM. Fieldwork: GSL and JOG. Data analysis: GSL. Writing – original draft: GSL, RB, and EM. Writing – review and editing: GSL, RB, and EM. All of the authors contributed to and discussed further analyses and commented on various versions of the manuscript.

    ACKNOWLEDGMENTS

    We thank the Postgraduate Program in Environment and Society (PPGA&S) at the University of Campinas for academic support. This work was financed by the São Paulo Research Foundation (FAPESP) through the project “After Hydropower Dams: Social and Environmental Processes Post-Construction in the Brazilian Amazon” (2019/17113-9), led by Dr. Emilio Moran. FAPESP also funded Guilherme Lobo’s PhD scholarship (2020/07037-0) and a Research Scientific Internship Grant (2022/13330-8) at the University of Stirling, UK, and Dr. Ramon Bicudo’s scientific grants (2022/16002-1 and 2023/15877-7). We also extend our gratitude to Silvia Mandai for permitting the use of her photograph taken at the Madeira River, to IEPEAGRO for sharing soil data, and to Dr. Thiago Sanna Silva and Dr. Mariluce Paes for their valuable suggestions. Finally, we are deeply grateful to all the ribeirinhos of the Madeira River for their participation and support.

    Use of Artificial Intelligence (AI) and AI-assisted Tools

    N/A

    DATA AVAILABILITY

    The data and code that support the findings of this study are openly available in the University of Campinas (Brazil) repository named Repositorio de Dados de Pesquisas da UNICAMP (REDU) at https://doi.org/10.25824/redu/1WTNAC. The data set consists of responses from anonymous semi-structured interviews, soil data, and R, Google Earth Engine, and Colab scripts. Ethical approval for this research study was granted by University of Campinas Ethical Committee (CEP: 61440222.9.0000.8142).

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    Corresponding author:
    Guilherme Lobo
    guisousalobo@gmail.com
    Fig. 1
    Fig. 1. Illustration of topographic gradients, water column variation, agricultural and extractivism practices, and vegetation in the <em>várzea</em> of the Madeira River. Source: Authors.

    Fig. 1. Illustration of topographic gradients, water column variation, agricultural and extractivism practices, and vegetation in the várzea of the Madeira River. Source: Authors.

    Fig. 1
    Fig. 2
    Fig. 2. Study area with river gauges used in hydrological analysis. Surveyed <em>ribeirinho</em> communities: Cujubim Grande, São Carlos, Nazaré, and Calama. Source: Prepared by the authors using data from IBGE (boundaries), ANA (gauges and dams), SEDAM-RO (communities), and Pekel et al. 2016 (hydrography).

    Fig. 2. Study area with river gauges used in hydrological analysis. Surveyed ribeirinho communities: Cujubim Grande, São Carlos, Nazaré, and Calama. Source: Prepared by the authors using data from IBGE (boundaries), ANA (gauges and dams), SEDAM-RO (communities), and Pekel et al. 2016 (hydrography).

    Fig. 2
    Fig. 3
    Fig. 3. Mean monthly Pardé coefficients (± standard deviation) for the Madeira River, a normalized indicator average monthly flow divided by the annual average flow, comparing pre-dam (1967–2012) and post-dam (2013–2022) at the Porto Velho and Humaitá gauges, from 1967 to 2022.

    Fig. 3. Mean monthly Pardé coefficients (± standard deviation) for the Madeira River, a normalized indicator average monthly flow divided by the annual average flow, comparing pre-dam (1967–2012) and post-dam (2013–2022) at the Porto Velho and Humaitá gauges, from 1967 to 2022.

    Fig. 3
    Fig. 4
    Fig. 4. Indicators of short-term flood pulse variability based on flow daily data (m3 s–1 day–1) from 1967 to 2022. Plots show pre-dam (1967–2012) and post-dam (2013–2022) mean (± standard deviation) for (a) flow rise rates, (b) flow fall rates, and (c) the number of flow reversals at gauges located 5 km (Porto Velho) and 250 km (Humaitá) downstream of the dam. Asterisks reveal significant differences between the pre and post-dam periods (Wilcox test, <em>p</em> < 0.05).

    Fig. 4. Indicators of short-term flood pulse variability based on flow daily data (m3 s–1 day–1) from 1967 to 2022. Plots show pre-dam (1967–2012) and post-dam (2013–2022) mean (± standard deviation) for (a) flow rise rates, (b) flow fall rates, and (c) the number of flow reversals at gauges located 5 km (Porto Velho) and 250 km (Humaitá) downstream of the dam. Asterisks reveal significant differences between the pre and post-dam periods (Wilcox test, p < 0.05).

    Fig. 4
    Fig. 5
    Fig. 5. Dimensionless hydropeaking indicator (HP1) for the Madeira River using hourly flow data from the Abunã gauge (green, upstream, non-impacted) and the Porto Velho gauge (red, < 5 km downstream of Santo Antônio dam, impacted). The indicator shows the hourly rate of flow change, calculated as the difference between maximum and minimum flow divided by the daily mean. The Wilcoxon test revealed a significant difference between impacted and non-impacted regions (<em>p</em> < 0.001).

    Fig. 5. Dimensionless hydropeaking indicator (HP1) for the Madeira River using hourly flow data from the Abunã gauge (green, upstream, non-impacted) and the Porto Velho gauge (red, < 5 km downstream of Santo Antônio dam, impacted). The indicator shows the hourly rate of flow change, calculated as the difference between maximum and minimum flow divided by the daily mean. The Wilcoxon test revealed a significant difference between impacted and non-impacted regions (p < 0.001).

    Fig. 5
    Fig. 6
    Fig. 6. (a) Bean, manioc, and squash plantations managed by <em>riberinhos</em> in the low <em>várzea</em> of the Nazaré community, September 2011. Photo by J. Gil taken during Institute for Agri-Environmental Studies and Research and Sustainable Organizations (IEPAGRO) fieldwork. (b) Illegal gold mining platforms on the Madeira River contrasted with a squash plantation in the high-<em>várzea</em> during the interviews (October 2023). Photo by S. Mandai.

    Fig. 6. (a) Bean, manioc, and squash plantations managed by riberinhos in the low várzea of the Nazaré community, September 2011. Photo by J. Gil taken during Institute for Agri-Environmental Studies and Research and Sustainable Organizations (IEPAGRO) fieldwork. (b) Illegal gold mining platforms on the Madeira River contrasted with a squash plantation in the high-várzea during the interviews (October 2023). Photo by S. Mandai.

    Fig. 6
    Table 1
    Table 1. Soil chemical parameters for 2011 and 2023 samples of each <em>várzea</em> topographic gradient (low and high <em>várzea</em>) in the <em>ribeirinho</em> communities located downstream of the Madeira Hydroelectric Complex, Porto Velho, Brazil.

    Table 1. Soil chemical parameters for 2011 and 2023 samples of each várzea topographic gradient (low and high várzea) in the ribeirinho communities located downstream of the Madeira Hydroelectric Complex, Porto Velho, Brazil.

    Chemical parameters Cujubim Grande São Carlos Nazaré Calama
    Low-várzea High-várzea Low-várzea High-várzea Low-várzea High-várzea Low-várzea High-várzea
    2011 2023 2011 2023 2011 2023 2011 2023 2011 2023 2011 2023 2011 2023 2011 2023
    pH 5.4 5.2 5.7 5.1 5.5 5.3 6.7 4.7 6.2 6 5.4 5.3 5.6 5.9 4.2 5.1
    P (mg/dm³) 45 15 30 21 86 18 80 84 79 50 75 21 83 27 3 21
    K (mmcolc/dm³) 2 1.1 1.2 1.9 1.9 1.3 2 0.4 3.6 0.6 3 0.8 2.3 0.6 0.7 1.9
    Ca (mmcolc/dm³) 51 40 48.8 17 72.4 17 60.5 18 15.5 18 18.9 17 63.8 15 2.2 17
    Mg (mmcolc/dm³) 27 16 24.2 7 31.2 8 34.2 3 5.1 4 6.4 14 24.8 5 1.8 7
    Al+H (mmcolc/dm³) 36.3 17 16.5 14 16.5 13 8.3 11 54.5 8 75.9 12 14.9 9 113.9 14
    MO (g/kg) 3 7 9.9 4 6.2 6 7.6 3 14.3 2 16.4 3 6.2 7 39.1 4
    V (%) 61 77 77 69 86 67 92 66 53 74 45 73 86 70 4 65
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    Home > VOLUME 30 > ISSUE 3 > Article 32 Research

    Nutrient deficit rather than distance of farming activities from the boundary of protected areas drives crop raids by elephants

    Chama, L., S. M. Siachoono, and D. Phiri. 2025. Nutrient deficit rather than distance of farming activities from the boundary of protected areas drives crop raids by elephants. Ecology and Society 30(3):32. https://doi.org/10.5751/ES-16116-300332
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    • Lackson ChamaORCIDcontact author, Lackson Chama
      Copperbelt University, School of Natural Resources, Department of Zoology and Aquatic Sciences, Kitwe, Zambia
    • Stanford Mudenda SiachoonoORCID, Stanford Mudenda Siachoono
      Copperbelt University, School of Natural Resources, Department of Zoology and Aquatic Sciences, Kitwe, Zambia
    • Darius PhiriORCIDDarius Phiri
      Copperbelt University, School of Natural Resources, Department of Plant and Environmental Sciences, Kitwe, Zambia

    The following is the established format for referencing this article:

    Chama, L., S. M. Siachoono, and D. Phiri. 2025. Nutrient deficit rather than distance of farming activities from the boundary of protected areas drives crop raids by elephants. Ecology and Society 30(3):32.

    https://doi.org/10.5751/ES-16116-300332

  • Introduction
  • Methods and Materials
  • Results
  • Discussion
  • Conclusions
  • Acknowledgments
  • Author Contributions
  • Acknowledgments
  • Data Availability
  • Literature Cited
  • agricultural crops; crop raid; elephants; food quality; natural vegetation
    Nutrient deficit rather than distance of farming activities from the boundary of protected areas drives crop raids by elephants
    Copyright © by the author(s). Published here under license by The Resilience Alliance. This article is under a Creative Commons Attribution 4.0 International License. You may share and adapt the work provided the original author and source are credited, you indicate whether any changes were made, and you include a link to the license. ES-2025-16116.pdf
    Research

    ABSTRACT

    Human-wildlife conflicts resulting from the raiding of agricultural crops by elephants are among the major challenges affecting the conservation of this flagship species. Several studies have pointed at human activities, such as farming nearer to protected areas boundaries, as the main driver of these conflicts. Studies comparing the quality of food between agricultural crops and the natural vegetation in the elephants’ natural habitats as the potential key driver of these conflicts, are almost non-existent. We tested if there were differences in the incidences of crop raids with distance of farming away from protected area boundaries. Further, we compared the food quality of agricultural crops to the natural vegetation in the mammals’ habitat in and around Kasanka National Park in Zambia. Surprisingly, there was no difference in the incidences of crop raids relative to the distance of farming away from the protected area boundary. Further, the results show higher protein, energy, and moisture composition in the often-raided agricultural crops than the natural vegetation. However, the natural vegetation had higher ash, vitamin C, and fiber composition relative to agricultural crops. Broadly, our results suggest that the natural vegetation in the wild may not necessarily have all the key nutrients in adequate proportions to meet the body requirements of elephants. Therefore, elephants raid the crops to compensate this nutrient deficit, irrespective of how far the farms may be situated from the boundaries of protected areas.

    INTRODUCTION

    Human-wildlife conflicts are increasingly becoming one of the major challenges affecting global conservation efforts. The problem is especially prominent in Africa and Asia, where many countries are host to a rich biological resources base, but are crippled with many challenges, among which include an ever-increasing human population (World Bank 2022; Suzuki 2019, World Bank blog, https://blogs.worldbank.org/opendata/worlds-population-will-continue-grow-and-will-reach-nearly-10-billion-2050), contention for space (Shaffer et al. 2019), struggles to balance economic development and nature conservation (El-Ashry 1993, Alexander and Whitehouse 2004, Cao et al. 2021), coupled with insufficient capacity to manage these resources (Hussain 2023). Large mammals like elephants (Loxodonta africana) have been shown to be at the heart of most of these conflicts (Naughton-Treves 1997, Quirin 2005, Wang et al. 2006a, Warren 2009), because their foraging behavior is characterized by expansive home-range needs (Karanth and Sunquist 2000, Fernando et al. 2008a, b), forcing them to compete directly with humans for limited space and resources (Goswami et al. 2014, Hoare 2015, Youldon et al. 2017, Shaffer et al. 2019).

    Human-elephant conflicts are further heightened by human activities that encroach on elephant habitat (Leimgruber et al. 2003, Acharya et al. 2017, Di Minin et al. 2021, Gobush et al. 2021), such as farming either close to the boundaries of protected areas or along wildlife migration corridors (Wang et al. 2006b, Linkie et al. 2007, Strum 2010, Fungo 2011). Over the years, these interactions have resulted into either the decimation of the mammal’s populations or destruction of their habitats by humans (Hance 2013). For example, the population of African elephants is said to have declined from 3–5 million to between 470,000 and 690,000 over the last 100 years, while that of the Asian elephant declined from 100,000 to between 35,000 and 50,000 in the same period, mainly due to habitat loss and conflicts with humans (WWF 2002). In countries such as India, Kenya, and Sri Lanka, up to 100, 120, and 200 annual elephant mortalities have been reported, respectively, resulting from conflicts with humans (MOEF 2010, Santiapillai et al. 2010, Fernando and Pastorini 2011, Shaffer et al. 2019).

    Human fatalities of varying proportions have also been reported across several countries (e.g., see Mariki et al. 2015, Köpke et al. 2024). With the projected further increase in human population (World Bank 2022; Suzuki 2019, World Bank blog), this will increasingly draw both elephants and humans closer to each other, and will potentially escalate the incidences of human-elephant conflicts (Leimgruber et al. 2003, Shannon et al. 2009, Das and Chattopadhyay 2011, Montez and Leng 2021). Therefore, unless a tangible solution is in place, this will continue to undermine elephant conservation efforts and may reciprocally result into substantial damage to human grown crops, threatening livelihoods, human life and property by elephants (Acharya et al. 2017, Shaffer et al. 2019, Eustace et al. 2022). However, addressing human-elephant conflicts also calls for the examination of evidence from a growing body of studies suggesting that these, often fatal, interactions are somehow triggered by the variation in the nutritional quality of food between agricultural crops and the vegetation in the mammals’ natural habitats (Sukumar 1990, Rode et al. 2006, Pokharel et al. 2019, Vogel et al. 2020; Vogel et al. 2019, unpublished manuscript). Generally, agricultural crops have been shown to have superior nutritional quality compared to the natural vegetation in the wild. This observation has been made in both Africa (e.g., Rode et al. 2006, Branco et al. 2019, Vogel et al. 2020; Vogel et al. 2019, unpublished manuscript) and Asia (e.g., Sukumar 1990, Pokharel et al. 2019), potentially suggesting that food nutrients composition (henceforth referred to food quality) is likely to be an important factor in driving the elephant’s optimal foraging behavior and patterns of habitat use, including the raiding of agricultural crops (Pretorius et al. 2012; Vogel et al. 2019, unpublished manuscript).

    Establishing the key drivers of human-elephant conflicts is essential if the future of these animals and the livelihoods of affected communities are to be ascertained. Certainly, food quality is critical in defining the fitness of wild animals (Nyambe et al. 2017). For example, some studies have shown that poor food quality could reduce the growth rate of an organism or even cause failure to reproduce or premature death (Chapman and Reiss 1992, Bolen and Robison 1995). Many wild herbivores in particular have long been shown to be largely limited by the availability of protein in their diet (Bell 1969), especially during non-growing seasons (Schmidt and Snyman 2010).

    Given that food quality of plants can be influenced by environmental parameters such as geographical location, climate, soil type, fertility, and moisture (Yang et al. 2018), it remains unclear as to what extent the food quality of agricultural crops will remain higher than that of wild vegetation. The influence of food quality could particularly be true in a country like Zambia, given that the raiding of human grown crops by elephants is more prominent in the growing season (Nyirenda et al. 2011), during which there is a comparable availability of food resources in both human farms and the elephant’s natural habitats (Clegg and O'Connor 2017). In this case, crop raiding is unlikely to be driven by the scarcity of food in the wild. Thus, studies on human-wildlife conflicts should not only focus on the location of agricultural fields away from the boundary of protected areas or wildlife migration corridors, but also on parameters of food quality and the role they could potentially play in driving elephants toward the raiding of crops. This may help generate information that could contribute toward finding a lasting solution to meaningfully reduce these conflicts.

    Food nutrients such as protein, energy, ash, moisture, vitamin C, and fiber have been shown to be particularly critical in the diet of elephants. For example, elephants tend to select foods that are high in protein, energy, and ash, albeit wild plants have been shown to be lower, especially in protein and minerals than agricultural crops (Sukumar 1989, Osborn 1998). Thus, as Rode et al. (2006) suggested, these differences in nutrient composition could be used by elephants to raid agriculture crops to supplement deficient diets in the wild (McDowell 1997). Moisture content of the food determines its quality prior to consumption, especially in the context of texture, taste, appearance, and freshness (AOAC 1995, Isengard 2001, Nyambe et al. 2017). Thus, its presence enhances the palatability of animal food. And adequate dietary vitamin C has been shown to act as an immunomodulatory agent, a critical prophylaxis especially for the prevention of several viral infections (e.g., Elephant endotheliotropic herpesvirus hemorrhagic disease) that often affect elephants (Mousavi et al. 2019). Further, Carr and Maggini (2017) have shown that vitamin C is important for stimulating neutrophil migration to sites of infection, where it enhances phagocytosis, oxidant generation, and microbial killing, whilst simultaneously protecting the host tissue from excessive damage, i.e., by enhancing neutrophil apoptosis and clearance by macrophages, and decreasing neutrophil necrosis and NETosis. Thus, the presence of vitamin C in the diet is necessary for the immune system to mount and sustain an adequate response against pathogens (Carr and Maggini 2017, Colunga et al. 2020). Obviously, dietary fiber plays an important role in the health of animals (Adiotomre et al. 1990, Prosky 2000, Montagne et al. 2003, Cummings et al. 2004, DeVries 2004). However, the overly disproportionate increase in fiber composition has been shown to trigger a significant decrease in the quality of animal food in the wild, as it leads to low moisture, protein, energy, and vitamin C composition (Pei et al. 2001, Nyambe et al. 2017). Thus, a higher dietary fiber diet could potentially lead to deficiencies in these critical nutrients (Schmidt and Snyman 2010) and has been shown to reduce subjective appetite, energy intake, and body weight in some animals (Wanders et al. 2011).

    The aim of this study is to increase understanding of the key drivers of human-elephant conflicts for enhanced conservation and ascertaining the livelihoods of affected or vulnerable communities. We tested if there is a difference in the incidences of crop raids by elephants at three distances (of farming) away from the boundaries of protected areas (namely, Kasanka National Park and the nearby wildlife migration corridor). Further, we compared the food quality of agricultural crops to the natural vegetation in the mammals’ habitat in and around Kasanka National Park in Zambia. We predicted that (1) the incidences of crop raids by elephants remained a major problem in our study area, potentially compromising the livelihoods of the majority of households and undermining elephant conservation efforts, (2) the escalation of human-elephant conflicts is not necessarily driven by the location of farming activities in proximity to either the boundary of protected areas or elephant migration corridors, as has been suggested by some studies, and (3) the food quality of agricultural crops is superior to that of the natural vegetation in the elephant’s habitats and this is likely to trigger the raiding of crops by elephants (McDowell 1997, Rode et al. 2006, Pretorius et al. 2012, Branco et al. 2019).

    METHODS AND MATERIALS

    Study area

    The study was undertaken in and around Kasanka National Park, a protected area located in the Central province of Zambia (12° 30′S, 30° 14′E; Fig. 1). The park, which hosts a population of approximately 50 elephants, is completely surrounded by the Kafinda Game Management Area (KGMA). The KGMA (3491 km²) shares boarders with the Bangweulu wetlands and Lavushi Manda National Park in the north, the Muchinka Chiefdom in the south, Mpika district in the east, and an international boundary with the Democratic Republic of Congo in the west. Both Kasanka National Park and Lavushi Manda National Park are currently under public-private partnership management regimes. Moreover, the two national parks share an elephant migration corridor. Situated at an elevation of 1200 m (approximately) above sea level, the area occurs in a predictably high rainfall region (1000 and 1300 mm annually). The rainfall activities are largely triggered by the Congo air-mass that moves south into Zambia. The area is characterized by a series of highly connected natural forest habitats stretching far-beyond the boundaries of the park into human farming areas. The vegetation is predominantly Miombo woodland, the largest forest type in Zambia, characterized by thin, nutrient-poor, and acidic soils, overlaying an iron-rich lateritic rock (Kennedy et al. 2008). The Miombo is dominated by leguminous trees, notably those of the genera Brachystegia, Julbernardia, and Isoberlinia. Traces of Chipya woodland also occur on deep soils in a few places (Smith et al. 2000, Smith and Fisher 2001). The area is also characterized by patches of evergreen swamp forest and is host to abundant wetland habitats, including perennial rivers as well as seasonal, permanent, and floodplain wetlands and lakes, especially toward the Chambeshi and Luapula Rivers further north (Byng 2008, Kennedy et al. 2008). These wetland habitats are partly connected or linked to the Bangweulu swamps, one of the largest marshes in the world and internationally recognized as a Ramsar site (Fig. 1). The most important water bodies in the KGMA are the Luapula and the Lulimala rivers, both sharing boarders with the Bangweulu wetlands. The Luapula River is the main source of water for the Congo River (Kennedy et al. 2008). Thus, the area is an important catchment area, endowed with a rich freshwater resource base. Effectively, this suggests that access to naturally existing water may not be a nutritional challenge for elephants and other animals existing within this ecosystem.

    The local people and livelihoods

    Host to a few clusters of sparsely populated human settlements, the area is home to the Bemba-Lala speaking people of Chief Chitambo’s chiefdom (Chama et al. 2023). The Chief owns the land and he is the supreme leader of the people locally, but subject to the President of the Republic of Zambia. The traditional leadership is decentralized into village clusters. Each cluster is led by a Chilolo (i.e., Chief’s cabinet minister representing each cluster) while villages are led by Village heads. The area is one of the remotest and most socioeconomically isolated in the country. Small-scale agriculture is the main occupation and source of livelihoods in the area (Eriksen 2004, Kennedy et al. 2008, Chama et al. 2023). Most of these farming activities are undertaken near the boundaries of Kasanka National Park while some occur along the elephant migration corridor linking Kasanka National Park to Lavushi Manda National Park. The distance between the two national parks is approximately 70 km.

    Field observations

    Between November 2017 and March 2018 and November 2022 and January 2023, fieldwork was undertaken both inside and outside Kasanka National Park.

    Monitoring elephants feeding inside Kasanka National Park

    In the park, fieldwork was characterized by the observations of elephants during their feeding activities to record and determine their food plant species preferences (i.e., following Chiyo et al. 2005, Koirala et al. 2016). These observations, which lasted for a period of two weeks, were conducted at six different sites, namely (i) Fibwe hide, (ii) Kabwe, (iii) Kafubashi dambo, (iv) Kapabi swamp, (v) Lake Wasa II, and (vi) Songa (Fig. 1). The observations were dependent on the total time that elephants took feeding at each site (lasting between 15 and 40 mins) before they moved out. Observations were repeated at least twice when elephants were seen revisiting each of these sites. Three observers, (accompanied by one game scout) were involved in physically tracking and observing the elephants inside Kasanka National Park. We then collected vegetation samples from all plants on which the animals were seen feeding in each site.

    Monitoring elephants feeding outside the park

    We repeated the observations outside the park to determine the food preferences of elephants when raiding agricultural crops, i.e., with the aid of camera traps (TOGUARD 2" Mini Trail Camera 20MP 1080P), following Berezin et al. (2023) and Davis et al. (2023). Here, we used camera traps because elephants often raided agricultural crops in late night hours, when most farm owners would be fast asleep, making it practically challenging to observe the mammals. Camera traps have been widely used to either identify individuals (Karanth and Nichols 1998, Silver et al. 2004) or investigate behavior that could be challenging to study using direct observations (Griffiths and van Schaik 1993, Smit et al. 2019). Six camera traps (i.e., three traps at each distance [2 km, 10 km, 20 km] from the protected area boundary) were placed on different days in each of six villages sharing borders with protected areas. Among these (six villages) included three off the boundary of Kasanka National Park (namely, Chalilo, Mapepala, and Mpelembe; Fig. 1) and another three off the boundary of the elephant migration corridor (namely, Chiundaponde, Kasamba, and Musangashi villages; Fig. 1). We used 20 km as the maximum distance because both African and Asian elephants have been estimated to travel an average of 5–10 km each day when living in non-extreme environmental conditions (Rowell 2014). Thus, we only expected this average distance to move to 20 km or beyond in extreme conditions or when elephants are lacking sufficient supplies of resources (e.g., food, water, etc.; Viljoen 1989, Spinage 1994). At each distance across villages, camera traps were placed in three randomly selected crop fields for a period of 72 hours before moving to the next village. We then took note of all crops on which elephants were recorded feeding in each field.

    Socioeconomic survey among communities living outside protected areas

    We conducted a socioeconomic survey in each of the six villages with the aid of semi-structured questionnaires (Appendix 1), interviewing communities (n = 108 households, comparable to Amwata and Mganga 2014) located at different distances (namely, 2 km, 10 km, 20 km) away from the Kasanka National Park Boundary (KNPB) and the elephant migration corridor (EMC) between Kasanka National Park and Lavushi Manda National Park. In each village, at least 15 farmers or household heads (i.e., ≥ 5 individuals at each distance) were randomly selected and interviewed in this survey. We recruited and trained five community enumerators who helped in administering the questionnaires to all selected household heads across villages. The surveys involved collecting information on the communities’ main sources of livelihoods, incidences of crop raids (i.e., the number of times their fields have been raided), and the type of crops grown. Further (and most importantly), the survey also verified with the local people if the types of crops on which the elephants were captured feeding (by the camera traps) are the most targeted on their respective farms. Similarly, food samples were collected from all crops verified by communities as most targeted by elephant raids.

    Handling and analysis of food samples

    In both Kasanka National Park and outside, at least 1 kg of vegetation sample was cut and collected with the aid of pruning shears. The samples (n = 48) were packed in kaki paper envelopes and weighed using a digital scale calibrated in grams. They were then stored in a cool box while they were transported from the field to the food chemistry laboratory at the University of Zambia within 48 hours of collection. At the laboratory, collected vegetation samples were subjected to food quality (protein, energy, moisture, ash, vitamin C, and fiber) analysis. Protein was determined by means of the Kjeldahl method and calculated using a conversion factor of 6.25% (Kjeldahl 1883, Levey et al. 2000, Latimer 2016, Mæhre et al. 2018). Energy content (kJ/g) was determined by exposing food samples to combustion at high pressure in bomb calorimetry (Rodríguez-Añón and Proupin-Castineiras 2005). Ash content (% ash) was determined gravimetrically via dry ashing of vegetation samples (approx. 100 g each) in a muffle furnace at 600 °C for 14 hour (Liu 2019). Vitamin C was determined by means of a high-performance liquid chromatography (RP-HPLC) with ultraviolet detection (Gazdik et al. 2008, Mazurek and Włodarczyk-Stasiak 2023), while total dietary fiber was determined by the enzymatic-gravimetric method and liquid chromatography. Here, each vegetation sample was subjected to extended enzymatic digestion at 37 °C to simulate human intestinal digestion followed by gravimetric isolation (Garbelotti et al. 2003, McCleary et al. 2010, McLeary and McLoughlin 2022).

    Statistical analysis

    During data analysis, we first used linear mixed-effects model fit by REML to test if the incidences of crop raids differed at varying distances (i.e., 2 km, 10 km, and 20 km) away from either KNPB or the EMC. Here, we used incidences of crop raids against distance as fixed effects, while distance nested in village name/location were used as the random effects. Secondly, we used analysis of variance to test if food quality differed among plant types or species (i.e., a variety of food plants on which elephants fed, inclusive of both agricultural crops and the natural vegetation in Kasanka National Park). In this analysis, plant type was used as a predictor while food quality (protein, energy, moisture, ash, vitamin C, and fiber) was used as the response. We then used the post-hoc test with Tukey Honest Significant Difference to tell if and where differences occurred in food quality among individual species of food plants. All the above statistical analyses were performed in R Version 3.0.2 (R Development Core Team 2006, Pinheiro et al. 2012). Socioeconomic data, which was largely centered on assessing the livelihoods and incidences of crop raids by elephants were analyzed with the aid of Microsoft excel (2013) following Amwata and Mganga (2014).

    RESULTS

    Livelihoods of the local people[1]

    Of the 108 household heads that were interviewed, 44% and 56% were female and male, respectively. The main sources of livelihoods in the area include small-scale crop husbandly (i.e. practiced by 98% [n = 106] of the population). Several crops are grown, but the most common and socioeconomically important crops (selected based on frequency of appearance on the list of crops given by farmers), are grown either as single (monocropping) or part of a cluster of several other crops grown simultaneously (intercropping) by individual households. These crops include maize (Zea mays, henceforth referred to as Agr1 [grown by 98% of the population]), cassava (Manihot spp., Agr2 [94%]), pumpkins (Cucurbita spp., Agr3 [54%]), ground nuts (Arachis spp., Agr4 [67%]), and sweet potatoes (Ipomoea spp., Agr5 [27%]), finger millet (Eleusine spp., Agr6 [25%]), and beans (Phaseolus spp., Agr7 [16%]). The majority (87%, n = 94) of the household-heads interviewed grew most of these crops for both food production and income generation. The income generated from the sale of these crop products is critical for supporting the well-being of these households in the area.

    Incidences of crop raids by elephants

    The mean frequency of incidences of raids in the EMC (2 ± 1) were similar to those in areas surrounding the KNPB (4 ± 1) during the past five years (F (1, 4) = 1.235; p > 0.05). Seventy-five (69.4%) of the households interviewed experienced incidences of crop raids by elephants on their farms. Among the crops grown by the local people, maize (Agr1; mentioned by 82%, n = 89 of the respondents), cassava (Agr2; 71%, n = 77), and pumpkins (Agr3; 54%, n = 58), respectively, were the most targeted by elephants. The number of individuals in each herd of elephants that was seen raiding crops ranged from 11 to 27 across villages. In the park, elephants were repeatedly seen feeding on four natural vegetation species, namely White thorn (Senegalia [Acacia] polyacantha; henceforth referred to as Wld1; number of elephant feeding visits [n = 14]), Rice grass (Oryzopsis spp.; Wld2; n = 11), Common reed (Phragmites australis; Wld3; n = 5), and Guinea grass (Megathyrsus maximus; Wld4; n = 13). Rice grass (Wld2) plants were particularly highly sought after by the mammals, albeit they could only be found in a couple of small clusters of swamps (Kafubashi and Kapabi areas) located in the middle of Kasanka National Park (Fig. 1).

    Effects of distance of farming activities on incidences of crop raid by elephants

    No difference occurred in incidences of crop raids across distances of farming activities away from either the KNPB or the EMC (F (2,102) = 1.80; p > 0.05; Fig. 2). Of all the elephant crop raid incidences recorded in the area (69.4%, see above), 29 (26.89%), 30 (27.78%), and 16 (14.81%) occurred within a radius of 2 km, 10 km, and 20 km, respectively, away from either the KNPB or EMC. Of the 26.89% incidences within the 2 km radius, 16 (55%) occurred in the KNPB while 13 (45%) occurred in the EMC areas. Of the 27.78% incidences that occurred in the 10 km radius, 18 (60%) occurred in the KNPB while 12 (40%) occurred in the EMC areas. And of the 14.81% that occurred in the 20 km radius, 9 (56%) occurred in the KNPB while 7 (44%) occurred in the EMC areas.

    Food quality across plant types

    The mean protein composition differed significantly across plant types (F (6, 41) = 33.39; p <0.0001; Fig. 3a). It was higher (per 100 g wet weight) for maize (Agr1; 4.02 ± 0.58%) than cassava (Agr2; 3.02 ± 0.27%), pumpkin (Agr3; 1.94 ± 0.51%), white thorn (Wld1; 1.61 ± 0.49%), rice grass (Wld2; 2.98 ± 0.17%), common reed (Wld3; 1.42 ± 0.27%), and guinea grass (Wld4; 1.64 ± 0.46%). Protein composition for cassava (Agr2) remained similar to rice grass (Wld2; p > 0.05), both of which were, however, significantly higher than the rest of the plants.

    The mean total ash content (per 100 g dry weight) differed significantly across food plant types (F [6, 41] = 21.12; p < 0.0001; Fig. 3b). Generally, it was higher among wild plants than agricultural crops. For example, ash content for white thorn (Wld1; 3.8 ± 0.94%) was higher than maize (Agr1; 1.57 ± 0.89%), cassava (Agr2; 1.43 ± 0.12%), and pumpkin (Agr3; 1.00 ± 0.27%). Similarly, the mean total ash content for rice grass (Wld2; 3.54 ± 0.44), common reed (Wld3; 4.12 ± 0.27%), and guinea grass (Wld4; 3.11 ± 0.40%) were each significantly higher than maize, cassava, and pumpkin. No difference occurred in ash content either among agricultural crops or among wild plants (p > 0.05).

    The mean moisture content (per 100 g wet weight) differed significantly across food plants (F [6, 41] = 41.29; p < 0.0001; Fig. 3c). It was higher for pumpkin (Agr3; 86.75 ± 3.26%) than maize (Agr1; 45.02 ± 10.81%), cassava (Agr2; 58.62 ± 2.35%), white thorn (Wld1; 47.42 ± 6.97%), rice grass (Wld2; 59.08 ± 8.91%), common reed (Wld3; 58.74 ± 5.60%), and guinea grass (Wld4; 59.98 ± 4.34%). No difference in moisture content occurred among the rest of the food plants (p > 0.05).

    Although the mean fiber content (per 100 g dry weight) for white thorn (Wld1; 3.25 ± 0.51%) and guinea grass (Wld4; 2.77 ± 0.32%) remained similar, both of them were generally significantly higher than the rest of the food plants, namely maize (Agr1; 1.64 ± 0.29%), cassava (Agr2; 1.88 ± 0.12%), pumpkin (Agr3; 1.72 ± 0.45%), rice grass (Wld2; 0.96 ± 0.15%), and common reed (Wld3; 1.76 ± 0.13%; F [6, 41] = 15.89; p < 0.0001; Fig. 3d). Besides being lower than white thorn and guinea grass, the fiber content for rice grass was also significantly lower than maize, cassava, pumpkin, and common reed.

    The mean energy content (per 100 g wet weight) differed significantly across food plant types (F [6, 41] = 57.66; p < 0.0001; Fig. 3e). It was higher for cassava (Agr2; 434.67 ± 26.31 KJ/g) than maize (Agr1; 212.32 ± 50.02 KJ/g), pumpkin (Agr3; 41.37 ± 14.78 KJ/g), white thorn (Wld1; 203.94 ± 68.26 KJ/g), rice grass (Wld2; 139.61 ± 21.46 KJ/g), common reed (Wld3; 146.39 ± 23.07 KJ/g), and guinea grass (Wld4; 136.42 ± 15.53 KJ/g). Although lower than cassava, the energy content for maize was significantly higher than both pumpkin and guinea grass. In fact, energy content for pumpkin was also lower than each of the remaining plant types (p < 0.05), i.e., besides cassava. However, no differences in energy content occurred among the rest of the food plant types (p > 0.05).

    The mean vitamin C content (per 100 g wet weight) differed significantly across food plant types (F [6, 41] = 27.0; p < 0.0001; Fig. 3f). It was higher for white thorn (Wld1; 113.74 ± 3.96 mg/g) than maize (Agr1; 71.37 ± 20.03 mg/g), cassava (Agr2; 0.77 ± 0.22 mg/g), pumpkin (Agr3; 82.35 ± 14.39 mg/g), and common reed (Wld3; 0.87 ± 0.06 mg/g). However, mean vitamin C content for white thorn remained similar with rice grass (Wld2; 92.65 ± 4.58) and guinea grass (Wld4; 92.30 ± 11.70) (p > 0.05).

    DISCUSSION

    Our results show that human-elephant conflicts remain a major problem in the study area, as nearly 70% of the households interviewed experienced several incidences of crop raids by elephants on their farms, which agrees with our first prediction. Secondly, the distance of farming activities away from the boundary of protected areas had no effect on the incidences of crop raids by elephants, as elephants raided all farms irrespective of how far they were located relative to the boundary of protected areas, and this is congruent with our second prediction. And although natural vegetation in the park had higher composition of ash, vitamin C, and fiber, our results show that it had comparatively lower composition of protein, energy, and moisture compared to agricultural crops, suggesting that the diet of elephants in the wild had a nutritional deficit in these nutrients. Thus, the elephants’ foraging decisions to raid agricultural crops could be largely driven by the need to increase their uptake of a diet rich in these elements, i.e., in line with our third prediction.

    Incidences of crop raids and livelihoods of the local people

    Clearly, human-elephant conflicts remain a major problem in the study area, as the majority of farmers still experienced several incidences of crop raids on their farms. Although several crops are grown, the major ones in the context of driving crop raids by elephants and sustaining the well-being of communities including maize, cassava, and pumpkins. The majority of these crops are predominantly grown for both income generation and as food sources by the local communities. The income generated from the sale of these crop products is the only source of income for the majority of households in the area, suggesting that any incidences of crop raids on the community’s fields by elephants could have significantly negative impacts on their livelihoods.

    Generally, communities that are dependent upon a single livelihood strategy have been shown to be particularly vulnerable in human wildlife conflict zones because of a lack of alternative income strategies (Dickman 2010, Shaffer et al. 2019, Anoop et al. 2023). For example, human-elephant conflicts were found to reduce household incomes among subsistence farmers by at least 35% in Kenya (Amwata and Mganga 2014), whereas in Tanzania, annual crop damage was equated to two months of household food loss, and reduced household cash income by 1.3% (Kaswamila et al. 2007). Similarly, elephant related conflicts cost communal farmers around US$1 million a year in Namibia, while in some Nepalese communities it can be up to around a quarter of the household incomes of poor farming families (WWF 2008). These and many other risks potentially explain why conflicts with elephants have driven many subsistence farmers (in both Africa and Asia) to either quit their settlements or stop growing food crops that attracts elephants to their farms (Dickman 2010, Barua et al. 2013, Amwata and Mganga 2014, Anoop et al. 2023). However, quitting or relocation of settlements often comes with costs, as farmers have to find or pay for new land to resettle and potentially construct new villages. Thus, unless locals are supported to venture into alternative income-generating activities (e.g., curio shops, village ecotourism, etc.), human-elephant conflicts can lead to socioeconomic deprivation and destitution among the affected communities, i.e., if left unaddressed (Dickman 2010, Barua et al. 2013). Worse still, these conflicts can compromise human appreciation for conservation of local biodiversity and undermine the potential especially for human-elephant coexistence (Hedges and Gunaryadi 2010, Graham et al. 2010, Barua et al. 2013, Anoop et al. 2023). Thus, for as long as the incidences of crop raids by elephants continue to occur in our study area, both the livelihoods (especially food security and household incomes) of the local people and the conservation of the elephants will remain under threat.

    Incidences of crop raids across distance of farming from protected areas

    Our results show that distance of farming activities away from either KNPB or EMC had no effect on the incidences of crop raids by elephants. These findings are in contrast to those from several previous studies (e.g., Andersson et al. 2013, Parker et al. 2014, Matseketsa et al. 2019) that have shown human-wildlife conflicts to have particularly been prominent among communities that either live or undertook their farming activities close to the boundaries of protected areas. In fact, other studies suggest that the incidences of crop raids by elephants were limited to within 4 to 6 km from the edge of protected areas (Gubbi 2012, Guerbois et al. 2012). However, the fact that these incidences remained similar across distances (i.e., up to 20 km) in our study area raises new questions about the correct radius of high-risk for the occurrence of human-elephant conflicts. On the one hand, our findings suggest that the maximum (20 km) distance threshold used in this study may not have been adequate to detect the effect of distance of farming activities (from the boundaries of protected areas) on crop raids by elephants. For example, elephants can walk up to 195 km per day (Elephants for Africa 2016), albeit they often only average between 5 and 10 km in non-extreme environmental conditions (Rowell 2014) and over 20 km in extreme conditions (i.e., on a daily basis; Spinage 1994, Viljoen 1989, Sukumar 2003, Leighty et al. 2009, Chiyo et al. 2014). Their movements are usually driven by a variety of factors, among which include the need for social groupings and also adjusting their foraging range relative to the distribution and availability of resources (McKay 1973, Whitehouse and Schoeman 2003, Slotow and van Dyk 2004, Leighty et al. 2009). Therefore, the 20 km (maximum) used in this study may fall within the normal daily threshold travelled by the mammals to forage for food resources. Thus, crop raid incidences were expected to remain unchanged within this distance.

    On the other hand, our findings could suggest that the distance of farming activities from the boundaries of protected areas may not necessarily be the key driver of human wildlife conflicts in our study area. Instead, other parameters, especially food quality (Osei-Owusu and Bakker 2008) may be responsible, as has been suggested by previous research (Nyhus 2016). In this case, the findings of the current research agree with our prediction that the escalation of human wildlife conflicts was not necessarily driven by the farms’ location relative to the boundary of protected areas, as has been suggested by previous studies (Andersson et al. 2013, Parker et al. 2014, Matseketsa et al. 2019). This may especially be true in our study area, given that it is a game management area that is host to a few clusters of sparsely populated human settlements and a series of highly connected natural forest habitats stretching far beyond the boundaries of protected areas into human farming areas. Potentially, these conditions provide a conducive environment for elephants to traverse and raid nutritious agricultural crops far from the edges of the protected areas. And the fact that these incidences remained similar between KNPB and EMC could be explained by the fact that farming activities by communities in both areas were centered on the growing of nutritionally similar combinations of crops. Thus, there was nothing unique between the two areas to trigger a different foraging behavior from elephants. Overall, our findings suggest that the distance of farming from the edge of protected areas is unlikely to affect crop raid incidences by elephants, as long as there is a connected forest habitat transcending the boundaries of protected areas into human farming areas and that the crops grown on those farms contain nutrients that are either lacking or inadequate in their natural habitats.

    Food quality and crop raids by elephants

    Although natural plants from the national park contained higher composition of ash, vitamin C and fiber, our results show that they were largely deficient of protein, energy, and moisture, i.e., compared to agricultural crops. Generally, these results seem to suggest that although elephants are able to obtain adequate supplies of minerals, vitamin C, and fiber in the natural habitat, there is a nutritional deficit where access to especially protein and energy was concerned. Thus, it is highly likely that the mammals’ foraging decisions to raid agricultural crops could be largely driven by the need to increase their uptake of a diet rich in these elements. Our findings are similar to those from research suggesting that nutrient deficiency in their natural habitats could be responsible for explaining the elephants’ dietary choices, among which include the behavior of consuming human grown crops (Sukumar 1990, Rode et al. 2006, Pretorius et al. 2012, Branco et al. 2019, Pokharel et al. 2019, Vogel et al. 2020; Vogel et al. 2019, unpublished manuscript).

    Although lower in composition among natural plants, protein, energy, and moisture are very critical in defining the survival of wild animals (Barboza et al. 2009). For example, besides being an important energy source (6 kcal/g; Robbins 1983), proteins are polypeptides of amino acids required for building of body tissues, albeit only ruminants (among herbivores) can synthesize a variety of amino acids with the help of symbiotic microbes in their rumen. Given that elephants are non-ruminant herbivores, they are unable to synthesize most of these amino acids. Thus, they need the presence of both qualitative and quantitative protein in their diet to increase their access to all essential amino acids (Branco et al. 2019). Although natural plants such as rice grass (2.98 ± 0.17g) has relatively comparable protein composition to agricultural crops like cassava (3.02 ± 0.27g), elephants still left the park to raid the latter outside the park. This could be explained by the assumption that a combination of both maize and cassava, which are often grown in abundance by the local people, provided a far much high protein composition than what the mammals could obtain from rice grass in the wild. Our findings agree with previous research that found cultivated crops to generally provide significantly more protein than wild vegetation (e.g., Sukumar 1990, Branco et al. 2019), ultimately suggesting that feeding on these crops provided the elephants with substantially more protein. In this case, crop raiding by elephants was an extension of their optimal foraging strategy.

    Alternatively, research has shown that several wild plants contain secondary compounds such as tannins that can impact negatively on the digestibility of protein (Barboza et al. 2009). Tannins bind to protein, rendering it unavailable for digestion (Clegg 2008). Therefore, it is highly likely that elephants could be driven to raid agricultural crops to avoid feeding on protein-rich wild plants because they contain secondary compounds, such as condensed tannins that act as chemical deterrents, as they negatively affect the ability of an animal to digest nutrients (Robbins et al. 1987). Elephants have also been shown to generally have poor digestive abilities (Greene et al. 2019). In African elephants, the digestion efficiency can be as low as 22% depending on forage quality (Clauss et al. 2003, Pendelbury et al. 2005, Greene et al. 2019). Given the potential presence of digestion inhibiting chemicals and toxins in their natural forage, elephants strategize their foraging behavior toward consuming a wide variety of plants to either meet their daily nutritional requirements or dilute the chemicals and toxins in some of the plants they feed upon to maximize protein digestion. Thus, this could partly explain their behavior to raid agricultural crops.

    Like protein, elephants have a high absolute energy requirement (Branco et al. 2019). The high energy requirement is driven largely by their large body sizes (Demment and van Soest 1985) and shorter gastro-intestinal tracts (GITs; i.e., in relation to their body sizes; Clauss et al. 2003, Clauss et al. 2005a, b), albeit the widths of their GIT are larger than expected (Clauss et al. 2003, Clauss et al. 2005a). These phenological attributes have been shown to effectively result in faster food passage rates, albeit with lower nutritional gains (Clauss et al. 2003, Clauss et al. 2005b, Muller et al. 2013). Clearly, however, elephants still constantly need abundant replenishment of energy to grow, reproduce, sustain metabolic demands, maintain their structures, and respond to changes in the environment (Benedict and Lee 1938, Dierenfeld 1994, Brown et al. 2004, Pretorius et al. 2012). Generally, they have a mixed diet (Cerling et al. 1999), which fluctuates across seasons (Codron et al. 2006, Owen-Smith and Chafota 2012, Shrader et al. 2012). Nonetheless, their high absolute energy requirements have been shown to drive the mammals to select plants of higher quality and digestibility so that energy intake can be maximized (Demment and van Soest 1985, Pretorius et al. 2012). Therefore, elephants may include plant species that are both most abundant and have the highest metabolizable energy value in their diet as in the case of some agricultural crops in our study area.

    Our findings are consistent with recent studies on patterns of crop raids by elephants in Africa that found agricultural crops to have exceedingly higher digestible energy than natural-forage diets (Nyhus 2016, Branco et al. 2019). Thus, elephants in our study area likely benefited considerably from crop raiding because of the significantly higher amount of digestible energy present in crops relative to the natural vegetation in protected areas. The above observations further agree with findings from other studies (Simpson and Raubenheimer 1993, Raubenheimer and Simpson 1997, 1999) suggesting that animals could adjust the amounts of food ingested from different food sources to keep the balance between different nutrients and consistently reach their daily nutrient requirements (Pretorius et al. 2012, Branco et al. 2019). Thus, this may explain the observed foraging decisions made by elephants to target and raid agricultural crops such as maize and cassava (outside their natural ecosystem), which are richer in protein and energy, respectively, than wild plants.

    Results from this study also show that pumpkin had a significantly higher moisture content than was found in wild plants. Moisture is arguably the most important nutrient in animal diets, as it is the medium through which many physiological process (e.g., metabolic processes, chemical reactions, eliminating waste from the body, etc.) are facilitated. Besides, it regulates temperature and this is particularly critical for large bodied and high-water consuming animals such as elephants (Barboza et al. 2009, Pretorius et al. 2012, Pontzer et al. 2020). Research has shown that the need for moisture or water in animals increases when they forage on a high-protein and high-energy diet, driven largely by a corresponding increase in metabolic waste, urinary excretion of urea, and heat produced by metabolism (Cherian 2020). Interestingly, our results show that besides pumpkins, elephants also targeted both maize and cassava that had significantly higher protein and energy contents, respectively, i.e., among the agricultural crops that they raided. Potentially, this suggests that the mammals feed on pumpkin to ensure that their metabolic processes were adequately supplied with the moisture to effectively break down a high protein and energy diet during crop raid.

    Generally, water intake in animals is also expected to increase with higher environmental temperatures and increased physical activity because of water lost through evaporative loss (Barboza et al. 2009, Dunkin et al. 2013, Pontzer et al. 2020). Essentially, water or moisture uptake should not really be a problem for elephants because their natural habitat (Kasanka National Park) has abundant naturally occurring perennial water bodies. Besides, crop raid incidences predominantly occur during the growing season, when most of these water bodies and the vegetation in the park are replenished from high annual mean precipitation (> 1300 mm) in the area. However, as elephants move several kilometers to raid agricultural crops, they possibly lose a lot of water, because most of these crops are located on farms outside protected areas and far from water bodies. Thus, they depend on moisture-rich crops such as pumpkins to compensate for their body water losses and to therefore maintain all water-related physiological functions.

    CONCLUSIONS

    Generally, human-elephant conflicts still remain a major challenge affecting a predominantly peasant farming-dependent community within Kafinda Game Management Area in Zambia. These conflicts are largely driven by the disparities in the quality of food in the elephant’s natural habitat, seemingly pushing them to raid highly nutritious agricultural crops in our study area. Broadly, these findings suggest that elephants can raid human grown crops, irrespective of the distance the farmland is located away from the boundaries of protected areas, provided such crops contain nutrients that are either lacking or inadequate in their natural habitats. Thus, human-elephant conflicts are likely to continue for as long as humans continue to grow crops whose food quality is higher than wild vegetation.

    These results do not necessarily support the practice of farming activities along or closer to the boundaries of protected areas by local farmers, as doing so undermines the integrity of these ecosystems, to the detriment of the wildlife species they host. Thus, farming activities should be undertaken outside the buffer zones (i.e., 10 km immediately after the boundary) of protected areas to promote both elephant conservation and the preservation of livelihoods for the local people. And given that most of the affected communities are farmers whose livelihoods are primarily derived from the raided crops, allowing this problem to continue is detrimental to the survival of these people. Therefore, policy makers should work in collaboration with researchers to identify appropriate measures to address this problem, especially in the face of these findings. Stakeholders (e.g., government, conservation, and charity NGOs, etc.) should especially support and work in collaboration with local communities to identify and introduce crops and livelihood strategies that are not susceptible to attacks by elephants. This will not only enhance the resilience of livelihoods and safety of human life, but also contribute toward the conservation of elephants. Further, we encourage more studies to test the effect of food quality of agricultural crops in driving crop raids by elephants to increase our understanding of the human-elephant conflicts dynamics and thereby be in a stronger position to address this problem for the benefit of both conservation and local communities.

    __________

    [1] All agricultural crops have been named with the letters Agr. (followed by a species’ unique number) while wild plants are named with the letters Wld. (followed by a species’ unique number).

    RESPONSES TO THIS ARTICLE

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    AUTHOR CONTRIBUTIONS

    LC originally conceived and formulated the research idea. LC assisted by SS undertook the fieldwork. DP did the mapping of the study area. LC analyzed the data. LC, SC, and DP wrote the manuscript.

    ACKNOWLEDGMENTS

    We thank the Department of National Parks and Wildlife (in Zambia) for the research permit and Kasanka Trust Limited for hosting us during fieldwork. This work was funded by the British Ecological Society small research grants for Africa.

    Use of Artificial Intelligence (AI) and AI-assisted Tools

    N/A

    DATA AVAILABILITY

    Data/code available on request because of privacy/ethical restrictions.

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    Corresponding author:
    Lackson Chama
    lackson.chama@cbu.ac.zm
    Appendix 1
    Fig. 1
    Fig. 1. Map of the study area. Dark green is Kasanka National Park, pale green is Kafinda and other game management areas (GMAs) where the local people live and grow their agricultural crops that are often raided by elephants. KNPB is the Kasanka National Park Boundary.

    Fig. 1. Map of the study area. Dark green is Kasanka National Park, pale green is Kafinda and other game management areas (GMAs) where the local people live and grow their agricultural crops that are often raided by elephants. KNPB is the Kasanka National Park Boundary.

    Fig. 1
    Fig. 2
    Fig. 2. The relationship between distance of farming activities from the boundary of protected area and the mean number of incidences of crop raids by elephants. The PA on the axis refers to the boundary of the protected area.

    Fig. 2. The relationship between distance of farming activities from the boundary of protected area and the mean number of incidences of crop raids by elephants. The PA on the axis refers to the boundary of the protected area.

    Fig. 2
    Fig. 3
    Fig. 3. Shows protein (a), ash (b), moisture (c), fiber (d), energy (e), and vitamin C (f) composition across both agricultural and wild plant types. Agricultural crops include maize (<em>Zea mays</em>, Agr1), cassava (<em>Manihot</em> spp., Agr2) and pumpkin (<em>Cucurbita</em> spp., Agr3). Wild plants include white thorn (<em>Senegalia [Acacia] polyacantha</em>, Wld1), rice grass (<em>Oryzopsis</em> spp., wld2), common reed (<em>Phragmites australis</em>, Wld3), and guinea grass (<em>Megathyrsus maximus</em>, Wld4).

    Fig. 3. Shows protein (a), ash (b), moisture (c), fiber (d), energy (e), and vitamin C (f) composition across both agricultural and wild plant types. Agricultural crops include maize (Zea mays, Agr1), cassava (Manihot spp., Agr2) and pumpkin (Cucurbita spp., Agr3). Wild plants include white thorn (Senegalia [Acacia] polyacantha, Wld1), rice grass (Oryzopsis spp., wld2), common reed (Phragmites australis, Wld3), and guinea grass (Megathyrsus maximus, Wld4).

    Fig. 3
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    Home > VOLUME 30 > ISSUE 3 > Article 31 Research

    The Great Stink in the 21st century? Problematizing the sewage scandal in England and envisioning a new infrastructure ideal

    Sylvester, R. E., P. Hutchings, and A. Mdee. 2025. The Great Stink in the 21st century? Problematizing the sewage scandal in England and envisioning a new infrastructure ideal. Ecology and Society 30(3):31. https://doi.org/10.5751/ES-16416-300331
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    • Ruth E. SylvesterORCIDcontact author, Ruth E. Sylvester
      School of Civil Engineering, University of Leeds
    • Paul HutchingsORCID, Paul Hutchings
      School of Civil Engineering, University of Leeds
    • Anna MdeeORCIDAnna Mdee
      School of Politics & International Studies, University of Leeds

    The following is the established format for referencing this article:

    Sylvester, R. E., P. Hutchings, and A. Mdee. 2025. The Great Stink in the 21st century? Problematizing the sewage scandal in England and envisioning a new infrastructure ideal. Ecology and Society 30(3):31.

    https://doi.org/10.5751/ES-16416-300331

  • Introduction
  • Theoretical Basis: Envisioning England’s Sanitation Future
  • Methodology
  • Results: Disjointed Progress Toward Sanitary Reform
  • Conclusions
  • Acknowledgments
  • Data Availability
  • Literature Cited
  • environmental health; ethnographic methods; public health; social imaginaries; water governance
    The Great Stink in the 21st century? Problematizing the sewage scandal in England and envisioning a new infrastructure ideal
    Copyright © by the author(s). Published here under license by The Resilience Alliance. This article is under a Creative Commons Attribution 4.0 International License. You may share and adapt the work provided the original author and source are credited, you indicate whether any changes were made, and you include a link to the license. ES-2025-16416.pdf
    Research, part of a special feature on The Next Wave in Water Governance

    ABSTRACT

    The Great Stink of 1858 saw politicians in the Houses of Parliament commission a new sewer system for London at an unprecedented scale and cost. Political consensus was driven by the stench emanating from the river Thames, filled with faeces. Today, England is experiencing parallels to the first Great Stink, with untreated sewage discharging into the country’s watercourses for a total duration of 3.6 million hours in 2024. The scale of sewer discharges has heightened tensions between the public and the water industry, with activists leading civic action that includes social media campaigns, bill boycotts, and street protests. We carried out an ethnographic study in the Yorkshire region with the aim of analyzing and exploring emerging tensions between stakeholders. We found that the root causes of the sewage problem were deeply contested, creating an uneven foundation for sanitary reform. Stakeholder groups understood the sewage crisis differently and were often found to be calling for competing solutions. To theorize these divergent problematizations, we draw from sanitation imaginaries literature that considers collective assumptions about waste infrastructures. Sanitary developments in England have long aspired to the modern sanitation ideal, seeking to discretely remove household waste waters, transporting and treating elsewhere, eliminating public health risk alongside minimal environmental impact. The contemporary sanitation crisis, or “Great Stink of the 21st century,” has shattered this modern infrastructure ideal and social imaginary, causing rifts between stakeholders about how and what progress can be made. Overall, historical parallels serve to remind that political consensus and a shared vision among stakeholders are necessary conditions for sanitary revolution in England.

    INTRODUCTION

    In recent decades, the matter of sanitation has been rendered invisible and conceived as uniform in England, in line with the modern infrastructure ideal. Yet the 2020 sewage scandal re-positioned sanitation as visible and revealed systemic ruptures across the network. Sewers are a form of faecal waste management, a service that can be delivered through an array of options and configurations, all with the primary purpose of ensuring environmental conditions favorable to public health (WHO 2018). Although sanitation terminology is not commonly used in England, we apply it in this research to recenter the primary purpose of sewers and to examine ingrained assumptions (or social imaginaries) around waste management.

    Most households in England have been connected to sewer networks since the mid-20th century (Hassan 1985). Although the common notion today is that all people are connected to these networks, there are notable exceptions. Certain populations remain unconnected and must employ alternative sanitation practices, including marginal social groups such as Roma and Traveller communities (Eminson 2024), boat dwellers (Sylvester and Underhill 2024), and people experiencing homelessness (Meehan et al. 2023). Despite these important minorities, this research is focused on the dominant narrative in England, premised on the ideal of modern, sewered service delivery.

    The late-19th century saw sweeping developments in clean water and sanitation provision, necessitated by populations and industry clustering around urban centers, producing intensely unsanitary environments (Abellán 2017). The Great Stink of 1858 recalls a summer when the river Thames became so putrid that politicians in the new Houses of Parliament, built on its banks, were driven to commission a sewer system for London at an unprecedented scale and cost (Halliday 2001). The chief engineer for the project, Joesph Bazalgette, is attributed with the skill and foresight that saved more lives than any public official of that era (Doxat 1977, Cook 2001). This is the most poignant example of sanitary reform in England, sparked by the proximity of those with power to a river of faeces, and a visionary engineer empowered with authority and financial resources.

    Sharing some parallels to the first Great Stink, in 2024 untreated sewage was discharged into England’s watercourses 450,398 times for a total duration of over 3.6 million hours (The Rivers Trust 2025). Whereas in the 19th century the construction of combined sewer networks enabled a revolutionary step change in sanitary conditions, in the 21st century this infrastructural design is channeling high volumes of sewage into the environment. Combined sewer overflows (CSOs) are system components that allow sewers to release excess untreated wastewater, designed only to operate under heavy rainfall events. However, new data show that, in many locations, this occurs during business as usual.

    Annual sewage spill data have been collected since 2016, via Event Duration Monitors (EDM) fitted onto CSOs, detecting changing wastewater levels and indicating sewage spills. In 2019 and 2020, EDMs were rolled out widely across the country, building national datasets that represent the scale of the issue. The Environment Act 2021 cemented the trends in open reporting, obliging water companies to publish their sewage data, moving away from the practice of private self-reporting (EA 2025). In the same year, results from a full assessment of England’s rivers were published, revealing that only 16% of surface water bodies were classified as in “good” ecological status, according to the Water Framework Directive Regulations (DEFRA 2025). Coinciding with the Covid-19 pandemic, lockdowns, and increased attention on the local environment, this time marks the beginning of the national “sewage scandal.”

    Since 2020, avid campaigners have mobilized, demanding rapid improvements to sewerage infrastructures and river health, making use of consumer power (bill boycotts; We Own It 2024), street protests (Gayle 2024), publicly available data (Sewage Map 2024), social media influencing (Save Windermere Campaign 2024), and leverage points in otherwise impenetrable water industry governance structures (discussed further in the “Competing geographies” section; Bullough 2022). Customer trust is at an all-time low (Consumer Council for Water 2024), political economists express the failures of privatizing water (Buse and Bayliss 2022), and seminal public health scholars ask: what will it take for a new sanitary revolution in the U.K. (Middleton and Saunders 2024)? Despite swathes of public attention (Usher 2023), progress toward sanitary reform is disjointed, riddled with contestation about what the real problem is and how it should be solved.

    We apply an ethnographic lens to this new iteration of the Great Stink, exploring these contestations and divisions between sanitation stakeholders (including those with an interest and role in sewer infrastructure, river management, and wider governance) ostensibly working toward the same goal. Drawing from critical geography and political ecology literature (McFarlane 2008, Lawhon et al. 2022), we attribute conflicting stakeholder narratives to distinct, high-level sanitation paradigms (or imaginaries), informing different formulations of the problem at hand. We find that two fundamental components of sustained, equitable sanitary reform are currently missing: clear political support and consensus on the future sanitation vision for England.

    THEORETICAL BASIS: ENVISIONING ENGLAND’S SANITATION FUTURE

    A defining feature of the first Great Stink was a strong aspiration for the future sanitary revolution: the efficient management and re-distribution of faecal waste away from populated areas. The “remote dumping of sewage and waste” is central to the contemporary urban process. Graham and Marvin’s (2001) seminal work on the modern infrastructure ideal argues that urban infrastructures are increasingly fragmented and politicized, often working to re-produce socioeconomic inequities in cities. Whereas the social imaginary of modern infrastructure is discrete, efficient, and universal, Graham and Marvin (2001) refute this through the lens of uneven and competing geographies.

    Analysis of the modern infrastructure ideal has been applied to specific sectors, such as Linton’s (2010) foundational text on modern water. In this research, we focus on the sanitation sector, examining how the modern sanitation ideal has become ingrained in England and a widely accepted social imaginary. However, the sewage scandal has ruptured this acceptance, based on widespread revelation of the uneven distribution of waste and its implications.

    Sanitation imaginaries

    We trace this sector-specific literature on the modern infrastructure ideal to McFarlane (2008) writing on the spatial imaginaries and logics of sanitation infrastructures in Bombay. He argues that ideologies of the “contaminated city” in the colonial period, and the “world city” in the postcolonial era, have shaped how sanitation has been implemented. The world city concept has connotations of being orderly, clean, and akin to other idealized cities in rich countries (McFarlane 2008). Similarly in Jakarta, Putri (2019) writes that geometric, urban layouts have been created in the image of western cities, re-producing belief in this type of logic.

    Building on McFarlane’s work, Morales et al. (2014) are the first to explicitly use the phrase “sanitation imaginaries,” defining it simply as the expectations people have for their sanitation. Participants in their study, from a marginal neighborhood in Buenos Aires, expressed beliefs around sanitation in a modern city. These included the expectations of state responsibility, and the absence of physical or mental engagement with excreta, which were seen as signifying “underdeveloped and backward lifestyles.” Further, the privacy associated with domestic sewerage was considered a marker of modern, urban citizenship (Morales et al. 2014).

    Adjacent literatures have also extended the concept of sanitation imaginaries. Jensen and Morita (2017) explore the ontologies of waste infrastructures using anthropological methods, finding that infrastructures are both created by and create “practical ontologies.” Sanitation infrastructures have the unique character of many secret, shameful, private, hidden, and unseen dimensions of modern society. As well as analyzing the spatial distribution of wastes in a city, anthropological insights help realize the potential for re-shaping social relations by looking at what happens in these spaces of visible waste (Jensen and Morita 2017, Alexander and O’Hare 2020).

    Most recently, Lawhon et al. (2022) offer a new type of sanitation imaginary as an alternative to the modern ideal. From their work in Kampala, they find that the promise of modernity, though still appealing, is waning. They propose modesty as an imaginary that rejects the hierarchy of modernity and “does not accept inadequate sanitation for some: it is founded (instead) on a vision of an interconnected city with shared interests” (Lawhon et al. 2022:161). A modest approach is relational, aware of the multi-scalar impacts of sanitation on the environment and wider society.

    Related scholarship exists in the Global North, with Silver (2019) extending relational theorization of urban inequality through decaying infrastructures in New Jersey. Meehan et al. (2020) disrupt common myths about modern water Global North contexts, and Picon (2018) examines how networked infrastructures are dependent on social imaginaries, through a case study of Haussmann’s renovation of Paris and the contemporary smart city perspective. England is one context that has, for decades, seemingly embodied the modern sanitation ideal, appearing to uniformly deliver sewered services to everyone at a similar quality and cost, under a highly neoliberal governance model (Lawhon et al. 2017). Yet, this appearance is waning and public belief in it is fracturing, in parallel to the visible degradation of sewer systems.

    Problematizing sanitation

    Attached to the absence of a clear sanitation vision is a lack of stakeholder consensus on what the real problem is. Bacchi and Goodwin’s (2016) problematization theory supports our analysis of contested understandings of the sanitation crisis. The term problematization represents how an issue is conceptualized and configured as a problem within social groups (Stengers 2019). Problematizing sanitation or wastewater management has shown to be used strategically to maintain political narratives and hide, disguise, or re-frame others (Weder 2022).

    In Sweden, Holmberg and Ideland (2022) find that wastewater management has been made into a public secret, upheld through a deliberate balancing act of visibility and invisibility. The problems associated with sanitation, such as leaks or sewer malfunctions, are presented to the public by water industry and political leaders as normal and treatable with the correct response and can be mitigated in the future by the correct behavior.

    Müller and Kruse (2021) study how drought is configured as a problem in Germany. They show this happening in several ways, such as through the legitimizing of political framings using scientific language, and the increasing use of a national security framing. Similarly, Bourblanc (2013) examines water pollution from agriculture in Brittany, finding that the local social movement constructs problems and changes them strategically to support their goals. Bourblanc (2013) also employs the concept of “problem ownership” that expresses the interest organizations have in controlling the problem definition in order to legitimize their involvement in solution-making processes.

    The literature on problematization and imaginaries demonstrates how deeply sanitation is intertwined with social behavior and ingrained, collective assumptions. These concepts underpin our investigation of the contemporary sanitation crisis, as we explore contested understandings of the root problem, and ask how we can move toward a consensus vision of a better sanitation future.

    METHODOLOGY

    Our methodological approach combines anthropological insights with a political ecology perspective of spatial inequities in our study region of Yorkshire. Although our findings are distinct to this region, they are also indicative of the broader situation in England.

    Data collection and research context

    We used the anthropological method of ethnography to gather data on experiences and beliefs around sewage and waste infrastructures. Ethnography requires extensive familiarization with the research context and interlocutors through observation, relationship building, and participation in local activities, as well as more formalized methods, such as semi-structured interviews. Our research was conducted over a period of 15 months, from September 2022 to December 2023. Ethical clearance was provided by the ethics committee at the University of Leeds, including a detailed data management plan and anonymity protocols.

    We began by closely following the developments of an activist group based in Knaresborough, who were responding to sewage discharges in their local river. Data collection activities in and around the town of Knaresborough included: observations at stakeholder meetings and local events, informal conversations, field notes, and reflections from personal river encounters.

    As the study progressed, we also established relationships with Ilkley, a nearby town in rural Yorkshire, and Bradford, a city of over 500,000 people (Figs. 1 and 2). These were developed by drawing on the researchers’ networks, attending local events, and connecting to local people and places of interest through university staff residing in the areas. Through these activities it became more apparent that the sewage crisis in Knaresborough was intertwined with regional dynamics. We attended river events in both Ilkley and Bradford, as well as conducting informal conversations and carrying out formal interviews.

    The rivers running through the two rural towns of Knaresborough and Ilkley are the Nidd and the Wharfe, respectively. Although distinct, the rivers have many similar qualities, deriving from head springs in the Yorkshire Dales National Park, home to Wild Brown Trout and Grayling, and dramatically gushing through the Nidd Gorge and The Strid (Wharfe) as well as meandering through rolling farmland. The rivers wind through the heart of both towns, adding to their picturesque natures. In contrast, the rivers in Bradford (the Bradford beck [a colloquial name for a small river or brook in northern England] and the river Aire) are substantially modified and covered over, and receive heavy inputs from sewer discharges and household misconnections. It is also a much more multi-cultural place than the rural Yorkshire towns, with immigrants from Eastern Europe and West India and Asia having settled in the city to work in the booming textile industry in the mid-20th century.

    Data analysis

    Alongside ethnographic data, the first author carried out 16 in-depth, semi-structured interviews with a range of sanitation and river stakeholders associated with the three research locations. Interviewees included representatives from river activists, wild swimmers, the water industry, the environment sector, regulators, politicians, and academics. In this paper, interviews are cited by the number they were assigned by the first author.

    Inductive thematic analysis was conducted on the qualitative data from interview transcripts and ethnography notes, documents, and articles. Braun and Clark (2006) establish a rigorous and theoretically flexible approach for qualitative thematic analysis. Informed by this, we chose to perform an inductive analysis to develop categories from the data itself (Fereday and Muir-Cochrane 2006). Bottom-up coding in this manner is never purely objective but rather related to the researcher’s prior knowledge, and as such we include a section below on positionality (Nowell et al. 2017). Five core categories were identified, reflecting common themes, patterns, and stories in the data. These categories were designed to retain some holistic sentiment and context behind each piece of data, so larger chunks of text were often added to a category first, before distillation. The core categories and their sub-categories are set out in Table 1.

    Once all relevant data had been attributed to a thematic category, each sub-category was reviewed and distilled to establish key findings. There was a large amount of data collected and analyzed, and in this paper we focus on only a portion of the data gathered on the contested nature of the problem between stakeholders (stakeholder perspectives and relationships) and the beliefs related to this (recurring stories and some data from valuing rivers). We also focus in this paper on the geographical differences across Yorkshire region, as we are writing a separate paper on the local dynamics of river activism in Knaresborough.

    Researchers’ positionality

    Carrying out an ethnography requires self-reflexivity and an awareness of one’s own position in relation to the interlocutors and the subject matter. This section demonstrates the authors’ reflection on their different relationships to this research.

    The three authors all live in Yorkshire, and as such have some degree of physical and social proximity to the research contexts and subject matter. The third author went to school in Knaresborough, grew up in a village close to the Nidd as it flows through the Vale of York, and has lived in the Aire Valley and swum in the Wharfe for the last twenty years. They bring a historical, situated perspective to the research. We recognize there is no one “community” or local relationship with these rivers; they are intertwined in multiple individual and collective dynamic relationships, which are continuously evolving.

    The first and second authors have moved to the city of Leeds in recent years from areas in the south of England because of their research positions at the University of Leeds. Being audibly southern adds a layer of social difference to interactions with some local people in the research contexts, a layer that has connotations of the “north-south” divide in England. There was often another sense of difference when talking with water industry representatives, deriving from the culture of the industry and created by the use of jargon and assumed prior knowledge. Once it became apparent that this knowledge was also known to the researcher, interlocutors settled more easily into a sense of familiarity.

    One dimension of our situated relationship to the research was a key entry point to the ethnography, through a member of the Knaresborough activist group, who also had links to the University of Leeds. Regarding their own positionality and place in this research, they wrote: “I went out of my way (a large amount of work and social capital) to make them (events and activities) happen. So, they didn’t just happen at grassroots level. At Ilkley too, half the residents are University of Leeds academics, so there is a huge resource behind the ‛grassroots’ campaign - unlikely to be a feature elsewhere” (I7).

    Overall, we reflect on multiple dimensions of positionality throughout the entire research process. The following section sets out our findings on different stakeholder views of the problem, what the causes are, and what the solutions could be.

    RESULTS: DISJOINTED PROGRESS TOWARD SANITARY REFORM

    The current sanitation problem in England is deeply contested, particularly between the most dominant stakeholders: activists, the water industry, and the environment sector. This creates uneven ground for progressing toward sanitary reform. Drawing from the problematization literature, we discuss how this problem is configured differently by stakeholder groups. We break down the broad problem of sanitation to focus on two key issues: sewer functionality and river health.

    Problematizing sewer functionality and river health

    In our study, most activists took the view that sewers were malfunctioning because of failures in sanitation infrastructure enabled by neglect, ignorance, over capacity, or deliberate action on the part of water companies. Additional blame was often attributed to failures of regulation, with one activist feeling that water companies are “a law unto themselves” because of a lack of river monitoring by the Environment Agency (EA), the environmental regulator for the water industry in England (I4). Another activist comment was aimed at Yorkshire Water and the economic regulator for the water industry, saying “[Y]ou’ve lied, and Ofwat let you get away with it” (I5).

    Activists’ problematization was commonly formulated around the passive failure of regulation and deliberate malice of water companies, who would rather pollute waterways than take a hit to shareholder profits. People in this stakeholder group arrive at this problematization from different water-related activities they enjoy participating in. For instance, wild swimmers value their physical connection to rivers, and in their activism they focus on human health impacts of polluted waters, often conflating this with wider river health. Anglers value their recreational time by the river, and are most concerned about fish stock and species. Although some activists do take a broader view than their predominant concern, many water industry and environment actors argue that holistic river health can only be measured by using multiple indicators.

    Environment sector representatives expressed concern over the focus on human health within activist problematization, as they felt this diverted attention away from holistic river health. Some even felt this focus exemplified modern anthropocentrism in approaches to river management. One interviewee from an environment non-governmental organization (NGO) commented that there needs to be improved “understanding (about) what human health requirements are, in terms of water quality (in rivers), versus what ecological requirements are... what people (think) are important, that’s what gets the attention. Sometimes it frustrates me because we should just care anyway” (I6).

    Other environmental actors faced opposition from activists when they shared knowledge regarding different aspects of river health, including agricultural runoff, off-grid sanitation, and industrial inputs. Many recounted being accused of “getting into bed with water companies” when sharing this in multi-stakeholder meetings (I6; I15; observations). Environment sector representatives also held a view of past and present societal influence on rivers, discussing how heavily humans have modified rivers throughout history, and how crucial it is to understand how we see them today. One interviewee asked, “Do you view rivers as wild ... or do you view (them) more as an almost continuation of a farmed managed landscape? You are trying to look after it in the one sense but you’re equally trying to use it as a resource, you know, and I think even in some legislation, there’s conflict” (I10). Another asserted that “an immense amount of social change” is required to improve river health, because “people perceive their rivers to be what they think they’re meant to be, [based on] how they’ve been brought up for generations” (I6).

    In terms of sewer functionality, environmental actors often problematized this through the lens of legislation and regulatory capacity. A recurring issue discussed was that water companies were allowed to “mark their own homework” regarding water quality testing at wastewater treatment plants, as well as a lack of spot-checking from the EA (I6; I16). Water industry actors also referred to regulation as problematic, although not from the perspective of holding them to account, but rather from the perspective of incentivizing (or not) changes to practice. The idea that, for water companies, ignorance is better than knowing the extent of sewer discharges is attributed to failure in regulation. One academic interviewee who had prior experience in the water industry argued, “[T]heir [water companies] job is to deliver on their regulatory obligations, and if the regulator doesn’t require them to know where that CSO is (then) that’s fair enough” (I3). Combined sewer overflows (CSOs) are components of sewer systems that allow the contents to spill out when the sewer is over full capacity. Important to note is that combined sewers funnel rainwater into sewage pipes, and are very common throughout England, as they derive from Victorian-era sewer design.

    The water industry broadly appeared to take issue with the activist narrative that sewers are malfunctioning, regularly asserting how CSOs are intentionally designed to spill during heavy rainfall to protect pipes backing-up in households, as well as attributing seemingly increasing discharges with new, climate-induced rainfall patterns (I14; I15; observations). Although these factors are a part of the story, other factors are not expressed by water industry representatives, such as real cases of overcapacity and underinvestment. Water industry representatives found generalized narratives like this frustrating because they hide the nuances and challenges they face, and yet they often followed the same approach, making generalizations about climate change or CSOs operating in an acceptable manner.

    One water industry interviewee emphasized how CSOs, when functioning properly, should not have any adverse environmental impact: “[I]f you’ve got an overflow and it discharges into the Humber Estuary and it’s a small volume, then the impact of that is gonna be absolutely negligible. And so you could have a huge overflow discharging into the estuary, but actually through modelling and through monitoring you can show that there is no harm” (I14). This argument was used to assert how the recent Storm Overflow Discharges Reduction Plan (DEFRA 2023) is unhelpful and ill-informed. The narrative has become part of water industry problematization about activist involvement, as many appear to feel that activists do not have adequate level of expertise to participate and do not recognize the work being done by the industry.

    Many in the water industry believe this reduction plan has been too heavily influenced by activists and is not conducive to fair and equitable change within the industry, particularly between companies:

    The other thing to remember as far as the companies is concerned is that that they are some of them in very different positions... United Utilities and Yorkshire (Water) have probably got nearly 2/3 of the entire CSOs in the sector... You have more separated systems in the South because you've had more new development. So you got more combined systems in the North because of, you know, old terraced housing. (I1)

    The plan was actively brought up in conversation by all interviewees from the water industry. The following sentiment was widely held: “[T]his latest episode is, in my experience, far and away the least well-informed response...that’s what politicians do, isn’t it? They respond (to) the narrative, rather than necessarily the technical evaluation” (I15).

    This discussion of different problematizations demonstrates some of the deep disagreements between stakeholders over what the problem really is. Activists focus on recent water industry practices, environmental sector representatives center river health from a holistic and historic perspective, and water industry representatives attribute the problem to inherited sewer designs and climate change. Relationships between many stakeholders are fraught, and the struggles between them restrict progress toward an integrated vision for sanitary reform.

    Competing geographies

    The concept that, since the sewage scandal, places in Yorkshire are now competing for attention and funding was a cross-cutting finding across different stakeholder problematizations. Seminal theory sets out the hidden reality of uneven infrastructures re-producing socioeconomic inequities, a reality hidden by the imaginary of modern infrastructure that is conceived as universal (Graham and Marvin 2001).

    A key argument from water industry representatives against activists taking a leading role in new regulations and political agendas is that it causes unequal distribution of funding within regions. This is because water companies in England are responsible for a given area of the country (a river basin area, closely related to geographical regions in England; for example, Yorkshire Water is broadly responsible for the Yorkshire region), and they finance infrastructure investments through billing customers in their area. The economic regulator, Ofwat, is mandated to ensure water companies provide efficient services at a fair price to customers. Ofwat permits a set rate of bills every five years and, as such, investments in a water and sanitation infrastructure are shared equally between all households in the area. Households are also unable to utilize standard consumer power by switching providers, so have very limited power to resist bill increases.

    We found that the origin of this competition argument derives from the success of Ilkley activists in receiving additional testing attention and sewer investment by applying to DEFRA (the central government’s Department for Environment, Food and Rural Affairs) to receive the first bathing water designation for an inland water body in England. This designation derives from European Union law and ensures additional water quality monitoring for places in which people are already bathing. An environment NGO representative called the Ilkley bathing water campaign an “absolute catalyst” for increasing attention on sewage from the environment and water sectors, emphasizing that “not everyone appreciates how much response and reaction the Environment Agency and Yorkshire Water had to do” after the campaign’s success (I6).

    In our research, it quickly became apparent that Ilkley’s bathing water application was highly contentious in the water industry and among regulators. The following quote from a water industry representative summarizes this general sentiment: “[W]hat it’s done is it distorted Yorkshire Water’s spending priorities. I think it is £80 million they’re throwing at Ilkley. I can think of much, much better places to spend £80 million. Places that would have a much greater impact on water quality and on public perception” (I15). This first instance of activists utilizing bathing water regulations not only leverages institutional resources but also re-shapes social relations, as explored in Jensen and Morita (2017), based on the spaces of visible waste in their local environment. This sociotechnical shift in Ilkley has direct implications for the Yorkshire region and, because of the town’s economic privilege, it can be criticized by those institutions it has leveraged.

    Some interlocutors from the environment sector (both NGOs and regulators) suggested that rural activists in Ilkley and Knaresborough were unhappy with their place low down on the investment priority list: “[T]he way for them to jump up that list is to do what they’re doing (apply for bathing water designation)” (I6). However, this priority list was often discussed abstractly, used to underpin the competing geographies argument, but was not publicly available to view. Further, in Bradford (a place with all the characteristics of being a high investment priority) people had not seen evidence of proactive investment or monitoring by Yorkshire Water. A member of a local river restoration group explained that they had taken 2000 photos over a 12-month period before Yorkshire Water would come and fix 50 sewer misconnections. Additionally, they discussed a recent £1.6 million fine Yorkshire Water received from the EA (EA 2024) because of a malfunctioning CSO, which they said the company knew about but chose not to report: “[I]f we hadn’t happened to be there trying to take a sample for something, it would have gone on for another year or so” (I16).

    In response to the bathing water success of Ilkley and the progress in Knaresborough, an interlocutor from Bradford commented, “Well, all power to them... it was a really clever move by the group in Ilkley. I just, I wish I’d thought of it, but that didn’t apply” (I16). Although water and environment representatives commonly raised concern over how bathing waters are creating regional inequality, our research in Bradford suggests that activists there are more focused on their local rivers, celebrating them in community festivals (Bradford beck festival 2023) and uncovering sections where possible, seeking to open urban rivers up to the public. Although they do not have the same scale of influence as Ilkley in terms of setting investment agendas and influencing political action (Ilkley Clean River Group 2025), it seems this is not something they are striving for. They are, however, striving for Yorkshire Water and the EA to take better care of their urban rivers.

    CONCLUSIONS

    Overall, analyzing stakeholder tensions by asking how they problematize the issue of sewage discharges reveals many layers of contestation. First, the root problem is understood differently, with activists problematizing through notions of passive regulatory failure and active water company malice. Environment sector representatives similarly acknowledge poor regulation, but attribute this to cuts in state government funding and weak legislation. They consider sewage discharges to be part of a bigger problem, where the public does not acknowledge or understand their holistic impact on the natural environment. Most water industry representatives see the problem of sewage discharges as resulting from climate change rainfall patterns and inherited combined sewer design they do not have the capacity or mobilizable funding to substantively rebuild. They are also very reactive to the problematization of activists, which has gained substantial media traction, and they feel portrays them unfairly.

    The root problem being so highly contested lays an unstable foundation for progressing toward sanitary reform. The solutions presented by stakeholders are themselves divergent, with environment representatives wanting to move toward holistic river health and nature-based solutions, water sector representatives desiring greater public trust to allow them to work through their expert priority investment list, and activists seeking to influence strong regulations to restrict the ability of water companies to neglect sanitation infrastructures.

    We suggest that underpinning these layers of contestation are fractured sanitation imaginaries, which have splintered off from the modern ideal. While scholars write on modern imaginaries, they do not prescribe their explicit characteristics, as these become materialized uniquely in particular contexts (Lawhon et al. 2022). One of the first steps in envisioning the future of sanitation in England is answering the question: what exactly has modern sanitation promised in this context, and in what ways has it failed to materialize?

    Stakeholders’ disappointment over this failure has led to a splintering of future ideals for sanitation, which are currently in competition. The environment sector envisions a future where people care about rivers as entities or beings in their own right and appreciate the interconnections between human life and river health. This may mean giving up some human desires to use the rivers as we please. Activists express a strong goal for a future where sewage is rarely, if ever, discharged into the natural environment, expressing the immorality of this practice and the ultimate responsibility of water companies as bill (or rent) collectors. The water industry is disappointed by the unrealistic expectations of activists and the wider public, but appear stuck in the challenges they face, lacking a clear vision of an achievable future.

    The Great Stink of 1858 showed that a sanitary revolution requires full political support and consensus vision for the future of sanitation. Although we focus on the aspect of vision, the role of the state is another crucial gap in this new iteration of the Great Stink. The high degree of sectorization and privatization in England has enabled the state to be complacent on this issue. Nonetheless, it retains ultimate responsibility for sustainable and equitable sanitation provision across the country as an essential service and a human right. In order to progress toward sanitary reform, we emphasize that both clear state support and a consensus stakeholder vision for the future are essential. The Great Stink in the 21st century has disintegrated the modern sanitation ideal in England, making the process of envisioning an incredible challenge, but one with revolutionary potential.

    RESPONSES TO THIS ARTICLE

    Responses to this article are invited. If accepted for publication, your response will be hyperlinked to the article. To submit a response, follow this link. To read responses already accepted, follow this link.

    ACKNOWLEDGMENTS

    The authors gratefully acknowledge the contribution of all interviewees and participants in the study, as well as the valuable inputs of the anonymous peer reviewers, and the editors for their hard work in producing this special issue. This work was supported by the Engineering & Physical Sciences Research Council [Grant Number EP/S022066/1].

    Use of Artificial Intelligence (AI) and AI-assisted Tools

    N/A

    DATA AVAILABILITY

    Anonymized interview transcripts will be made available in the open access White Rose research repository, as agreed with the University of Leeds’ ethics and data management committees. Raw ethnographic data (field notes, observations, informal conversations) cannot be made publicly available given the sensitive nature the research and the risk of identifiability of interlocutors.

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    Corresponding author:
    Ruth Sylvester
    r.sylvester@leeds.ac.uk
    Fig. 1
    Fig. 1. The Yorkshire Region situated in a map of England (source: Google Maps).

    Fig. 1. The Yorkshire Region situated in a map of England (source: Google Maps).

    Fig. 1
    Fig. 2
    Fig. 2. The Yorkshire region in detail, showing major cities. The research locations are shown in orange (Knaresborough), pink (Ilkley), and blue (Bradford). (Source: Google Maps.)

    Fig. 2. The Yorkshire region in detail, showing major cities. The research locations are shown in orange (Knaresborough), pink (Ilkley), and blue (Bradford). (Source: Google Maps.)

    Fig. 2
    Table 1
    Table 1. Thematic categories used to analyze interview and ethnographic data.

    Table 1. Thematic categories used to analyze interview and ethnographic data.

    Core categories Description
    Bathing water sites Data added to this category pertained directly to the specific issue of bathing water sites, a legal status granted by central government that officially designates a water body as one in which people bathe. This comes with certain benefits, such as increased attention and water quality testing. It is the crux of many new activist strategies in England.
    Five sub-categories were attributed: application process; Ilkley group; national picture; regional equity; role of citizen science.
    Recurring stories Data added to this category expressed similarities between interlocutors’ understanding of the problem of sewage discharges, and their beliefs about why it is happening.
    Two sub-categories were attributed: national stories; place-based stories.
    Stakeholder perspectives This category was for grouping common points of view on the problem of sewage discharges, found among certain stakeholders.
    Eleven sub-categories were included for all different stakeholders represented: academics; activists; agriculture; communities; government; media; politicians; regulators; rivers trusts; universities; water companies.
    Stakeholder relationships (with one another) This category was for grouping how different interlocutors reported feeling about other stakeholders, as many relationships were regularly discussed in interviews and ethnographic data.
    Four sub-categories were created for the ways in which these relationships were enacted and felt: beliefs about others’ motivations; blame; direct interactions; expectations of others.
    Valuing rivers Data added to this category captured what is it interlocutors valued, appreciated, felt and noticed about rivers.
    Five sub-categories were attributed to distinguish the specific ways in which people valued rivers and why this was an emotive subject: collective experiences with rivers; how “should” things be; individual experiences with rivers; visibility of pollution; what is “wrong.”
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    Home > VOLUME 30 > ISSUE 3 > Article 30 Research

    Perceptions of governance and access in artisanal marine fisheries in northern Brazil

    Dahlet, L., R. S. L. Barboza, I. E. van Putten, A. Akpan, R. Siriwardane-de Zoysa, and M. Glaser. 2025. Perceptions of governance and access in artisanal marine fisheries in northern Brazil. Ecology and Society 30(3):30. https://doi.org/10.5751/ES-16389-300330
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    • Lol DahletORCIDcontact author, Lol Dahlet
      Leibniz Centre for Tropical Marine Research (ZMT), Bremen, Germany; Institute of Geography, University of Bremen, Bremen, Germany; Grupo de Estudos Socioambientais Costeiros (ESAC), Universidade Federal do Pará (UFPA), Bragança, Brazil
    • Roberta Sá Leitão BarbozaORCID, Roberta Sá Leitão Barboza
      Grupo de Estudos Socioambientais Costeiros (ESAC), Universidade Federal do Pará (UFPA), Bragança, Brazil; Bolsista Produtividade CNPq; Fundação Joaquim Nabuco (DIPES-FUNDAJ), Recife, Brazil
    • Ingrid E. van PuttenORCID, Ingrid E. van Putten
      Wageningen University, Wageningen, The Netherlands
    • Aniekan Akpan, Aniekan Akpan
      Leibniz Centre for Tropical Marine Research (ZMT), Bremen, Germany; Institute of Geography, University of Bremen, Bremen, Germany
    • Rapti Siriwardane-de ZoysaORCID, Rapti Siriwardane-de Zoysa
      Bonn Center for Dependency and Slavery Studies (BCDSS), University of Bonn, Bonn, Germany; German Institute of Development and Sustainability (IDOS), Bonn, Germany
    • Marion GlaserORCIDMarion Glaser
      Leibniz Centre for Tropical Marine Research (ZMT), Bremen, Germany; Institute of Geography, University of Bremen, Bremen, Germany

    The following is the established format for referencing this article:

    Dahlet, L., R. S. L. Barboza, I. E. van Putten, A. Akpan, R. Siriwardane-de Zoysa, and M. Glaser. 2025. Perceptions of governance and access in artisanal marine fisheries in northern Brazil. Ecology and Society 30(3):30.

    https://doi.org/10.5751/ES-16389-300330

  • Introduction
  • Methods
  • Results
  • Discussion
  • Conclusion
  • Author Contributions
  • Acknowledgments
  • Data Availability
  • Literature Cited
  • Brazilian Amazon; fisheries governance; participatory network mapping; theory of access
    Perceptions of governance and access in artisanal marine fisheries in northern Brazil
    Copyright © by the author(s). Published here under license by The Resilience Alliance. This article is under a Creative Commons Attribution 4.0 International License. You may share and adapt the work provided the original author and source are credited, you indicate whether any changes were made, and you include a link to the license. ES-2025-16389.pdf
    Research

    ABSTRACT

    Artisanal fisheries form the basis of the livelihoods of millions of people in the Brazilian Amazon. Few empirical studies have characterized, however, how the governance of marine small-scale artisanal fisheries (SSF) in the Amazon, under the decentralized governance system in place, is perceived by those most affected. Drawing on Ribot and Peluso’s (2003) Theory of Access eight net-map interviews were conducted with key informants (small-scale and large-scale artisanal fishers, representative of civil society organization and public authority) to investigate how the local fisheries governance system is perceived to affect SSF access to fish and fisheries in Bragança (E of Pará, northern Brazil) between November 2022 and March 2023. Interactions are predominantly seen to occur between SSF as part of daily access negotiation processes. These processes take shape through interactions relating to knowledge of the biogeophysical environment and fishing, and conflict situations when customary fishing rules are not respected. Public authorities were seen to primarily control fishers’ legal access through inspections. Civil society organizations were perceived to be ineffective in facilitating access to benefits from public policies. Public authorities and civil society organizations were seen to leave a governance gap in terms of access for fishers. Vessel owners and post-harvest actors were seen by fishers as key regulators of SSF access to capital and markets. They control credits, set ex-vessel prices, and provide material resourcing that sustain power asymmetry. This study highlights key stakeholders’ perceptions of the range of relationships through which access to fish and fisheries is negotiated and contested. Our findings suggest that coastal fisheries governance in the Brazilian Amazon needs to address a number of factors influencing SSF, and more broadly, artisanal fishers’ access. This should occur alongside resolving immediate conflicts, with a consistent focus on equity and justice as systemic preconditions for sustainable human-nature relations in fisheries.

    INTRODUCTION

    Coastal and marine fisheries play a significant role in the livelihoods of Amazonian riverine and coastal communities. Fish and fishing are locally important for a protein-rich diet (da Silva and Begossi 2009, Isaac and de Almeida 2011), culture (Cordeiro 2010), and social dynamics (Mertens et al. 2015), and are often the sole source of income for local populations in coastal communities (Krause and Glaser 2003). In 2019, total marine catches along the Brazilian Amazon coast were estimated at 272,155.422 tonnes representing approximately 37% of the estimated national production (Page et al. 2020). Brazil has not collected national-level fishing statistics since 2011. Page et al. (2020) reconstructed fisheries landings using unpublished data from Freire et al. and data from the Food and Agriculture Organization of the United Nations (FAO) up to 2017. See Santos et al. (2023) for further discussion on the causes and implications of the lack of systematic national fisheries data collection.

    Marine fisheries in the Brazilian Amazon also contribute to national and international markets, with red snapper (Lutjanus purpureus) as an emblematic, although unsustainable, industrial, and large-scale artisanal export-oriented fishery (Isaac et al. 2009, Mescouto et al. 2024). Pará is the Brazilian state with the second highest number of fishers, of which around half are women (MPA 2023).

    Brazilian marine fisheries have undergone significant transformations in recent decades. In Pará, for instance, the once-prominent industrial fishing fleet has declined, and a large-scale, capitalized artisanal fleet has emerged (Isaac-Nahum 2006). This shift has altered local fishing relations by facilitating the entry of new actors, accelerating processes of elite capture, and deepening inequities in access to fish and fisheries (Maneschy 1990, McGrath et al. 2015). The 1988 Brazilian Constitution aimed to decentralize fisheries governance in Brazil with the ultimate goal of improving aspects of governance such as civil society participation, greater consideration of local realities, and local accessibility of public authorities (Wever et al. 2012). However, the governance of marine fisheries in the Amazon continues to be described as partially centralized (Oviedo and Bursztyn 2017), ineffective and weak due to institutional fragmentation, rule breaking and weak enforcement (Isaac and Ferrari 2017, Alencar et al. 2022), although with little empirical evidence so far. There are also assumptions, yet to be substantiated, that fisheries conflicts are relatively low in small-scale fisheries (SSF) because informal rules would help prevent them (Isaac et al. 2009). However, conflicts in the region have been found to arise from negative perceptions of protected area management (Prado and Seixas 2018, Borges et al. 2021), coercive behavior of fisheries surveillance agents, overlapping fishing grounds (Jimenez et al. 2019), and land distribution issues (Santos et al. 2020), among others. A common denominator of these conflicts is unequal access to fish and fisheries as a fundamental driver (Ribot and Peluso 2003, Saunders et al. 2024).

    In this study, we understand small-scale fisheries (SSF) as involving fishers fishing “autonomously or in a family economy, with their own means of production or through a partnership contract, ashore, or with the use of small boats” (translation of the definition of artisanal fishing in article 9, of the Brazilian National Policy for the Sustainable Development of Aquaculture and Fisheries Law No. 11.959, of June 29, 2009). Small-scale fisheries can have subsistence and/or commercial purposes. In large-scale artisanal fisheries, fishing trips last longer than 10 days, vessels are longer than 12 meters, and the hull is mostly made of wood (but can also be made of iron; Isaac et al. 2009). Importantly, we acknowledge that the legal definition of artisanal fishing varies across Brazil’s regulatory frameworks. For example, Law No. 11.959/2009 increased the vessel size limit from 10.2 to 20.3 metric tonnes. However, some regulations, notably those concerning social security, continue to use the previous 10.2 metric tonnes threshold, which leads to inconsistent classifications that affect fishers’ access to public policy benefits.

    Understanding how access is negotiated, achieved, or lost, is essential for socioeconomic outcomes and for the anticipation and more nuanced assessment of fisheries-related conflicts. In addition, a more precise understanding of the role of different groups and institutions in the structure and dynamics of fisheries governance, from the perspective of those whose lives are intimately affected by it, is essential for the formulation of strategies aimed at more equitable governance and governance outcomes.

    The present research investigates local and regional stakeholder perceptions of the governance structures and processes for coastal and marine fisheries in the Brazilian Amazon. The main objective is to understand how governance structures are perceived to influence SSF access to fish and fisheries in the coastal state of Pará, North Brazil. Specifically, the aim is to understand (1) who the main actors are in the perceived interaction networks; (2) what are the interactions that connect them; and, (3) how is access to fish resources and fisheries negotiated.

    Our analysis unfolds in two steps. First, we examined the composition of perceived networks in terms of actors and links. We then built on a thematic analysis of the conducted interviews to understand how different interactions relate to issues of access in SSF. We discussed the main implications for fishers’ access to fish and fisheries considering the Theory of Access (Ribot and Peluso 2003, Peluso and Ribot 2020). We looked at the Amazonian coast of Brazil as a case in point, in which the artisanal fishing sector has historically developed in the absence of supportive public policies and with unregulated market for fish (McGrath et al. 2015, Doria et al. 2021).

    Concepts and theoretical framework

    Governance and network mapping approaches

    We adopted Mark Bevir’s (2012:3) definition of governance as “all processes of social organization and social coordination.” Bevir (2012) pointed out that the rise of this concept is indicative of a certain discrediting of traditional political institutions. Framing these social organizational processes through the lens of governance shifts the focus away from traditional hierarchies and state structures, emphasizing instead the influence of markets and diverse network structures. In fact, “markets and networks might provide governance in the absence of any significant government” (Bevir 2012:3, but see also Young 1992), beyond the reading of governance as equivalent to government. This paradigmatic shift is also illustrated by the sharp increase in studies on environmental governance using social network analysis (Schwenke and Holzkämper 2020).

    Various approaches within the social sciences have highlighted the dynamics of networked governance. The social capital literature emphasizes how diverse actors are connected through a set of relationships, or ties, such as the exchange of lease quotas in the Tasmanian lobster fishery (van Putten et al. 2011), cooperation and information sharing among small-scale fishers in Lobitos, Peru (Maya-Jariego et al. 2017) in which varying network structures are acknowledged to influence actors’ access to different types of resources. This resonates with Ostrom’s theory of the commons (Ostrom 2010) and related work on collective action, which highlight how resource users, such as small-scale fishing communities, develop local governance arrangements to manage shared resources, sometimes in coordination with, or in the absence of, effective state involvement. Relational approaches (Emirbayer 1997) have recently gained traction; these adopt a process-relational understanding of sustainability-oriented themes. This implies transcending rigidly separate categorizations of human and non-human actors or actants all of which are perceived as having strong influence on how environmental governance unfolds (West et al. 2020).

    A number of studies have employed participatory network mapping or related approaches in the context of marine and coastal governance in Brazil. Glaser et al. (2018) adapted the Net-Map method (Schiffer and Hauck 2010) in a comparative analysis of fisher and tourism operator perceptions of environmental governance of a coral reef system in Northeast Brazil. Findings indicate that rules are more readily implemented if perceived as equitable and legitimate by those expected to comply. Gerhardinger et al. (2022) showed how the same methodological approach conducted with high-level institutional innovators of the Brazilian government can help to develop pathways for more transformative ocean governance.

    Access

    One objective of the study of environmental governance is to understand how access to natural resources and derived benefits are negotiated, contested, and distributed. Access is defined as “all possible means by which a person is able to benefit from things” (Ribot and Peluso 2003:156). In this study, we define “things” as fish and fisheries, where fisheries refer to the range of activities that can lead to the capture of specific fish resources and that can be defined by a variety of social, technological, economic, environmental, and governance conditions (Johnson 2006, Damasio et al. 2016, Smith and Basurto 2019). Similar to Silver and Stoll (2019), our analytical focus underscores that the benefits of fishing extend beyond mere production and income, highlighting its tangible contributions to sustainable livelihoods.

    Analyzing access relationships, i.e., who is seeking access, who is maintaining access, and who is controlling others’ access, provides a relational perspective on patterns of distribution and drivers of resource conflict. The Theory of Access (Ribot and Peluso 2003, Peluso and Ribot 2020) posits that beyond property rights, de facto gaining, maintaining, or controlling access to resources is regulated by a range of interacting mechanisms that fall under the following categories: technology, capital, markets, labor and labor opportunities, knowledge, authority, social identity, negotiation of other social relations, and legal- and illegal-based mechanisms. A short description of each mechanism is provided in Table 1. All operate through social relations in a dynamic way, and their workings are contingent on the power relations prevailing among involved entities.

    Peluso and Ribot (2020:300) argued that “[...] all efforts to gain, maintain, or control access are, at base, struggles in the domain of social relations [...]”, thus suggesting that negotiations of access are central to fishery-related conflicts. A growing number of studies point at lack of equity as a key underlying driver of marine conflicts (Glaser et al. 2018, Saunders et al. 2024). By illuminating the ways in which different groups of people do or do not benefit from a particular natural resource, and by detailing the benefits derived or pursued, the Theory of Access offers a framework to analyze the origin of environmental conflicts. Although mostly applied to terrestrial cases (Myers and Hansen 2019), this theory has also been useful to analyze issues of marine governance (Hicks and Cinner 2014, Calderön-Contreras and White 2019, Andriamahefazafy and Kull 2019). We suggest that these studies may not fully capture the relational component central to the Theory of Access. We propose and use a participatory network mapping methodological approach to assess how access is produced, negotiated, and contested through social interactions (Peluso and Ribot 2020).

    METHODS

    Study area

    This fisheries study focuses on the municipality of Bragança (Fig. 1), located on the coast of the state of Pará, in northern Brazil. Pará is Brazil’s second largest state and belongs to what is called the Legal Amazon. The Legal Amazon was initially established by Law No. 1.806 of 6 January 1953, which created the Amazon Economic Valorization Plan and designated the area as a region under the jurisdiction of the Superintendence of Amazon Development (SUDAM). Currently, the Legal Amazon encompasses approximately 58.9% of the Brazilian territory (https://www.ibge.gov.br/geociencias/informacoes-ambientais/geologia/15819-amazonia-legal.html?=&t=o-que-e). Both Pará and the municipality of Bragança have a medium-level human development index (HDI), which translates to poor levels of education, health, and revenue (https://cidades.ibge.gov.br/brasil/pa/braganca/panorama). Of the 393,512 fishers formally registered in Pará (MPA 2023), 194,184 are women and only 236 of them are classified as industrial fishers. In 2022, 49.8% of the 123,082 inhabitants in Bragança earned less than half the legal minimum monthly salary (https://cidades.ibge.gov.br/brasil/pa/braganca/panorama). The city and region lack adequate sanitation and drinking water systems, public recreational areas, health centers, and other infrastructure (Gomes et al. 2009, Gorayeb et al. 2009). This setting of poverty for the majority contrasts with the abundance of nature as local people often acknowledge (Isaac et al. 2010). In fact, this perception of natural abundance influenced the migration of people who fled the semi-arid climate of Northeast Brazil, especially the state of Ceará to come to this region since the late 1890s and early 1900s (Lacerda 2006). Among them, two early families founded what is now known as Vila dos Pescadores and Vila do Bonifácio. In 2010, the total population of Vila do Bonifácio (Fig. 1) was estimated at 1050 people (IBGE 2010, as cited in dos Santos Cavalcante et al. 2022), with 81% of families engaged in commercial artisanal fishing. In these and other fishing communities, kinship plays a crucial role in shaping access (Alencar et al. 2014).

    The study area embraces two Brazilian Ramsar sites, namely the Amazon Estuary and its mangroves and the Cabo Orange National Park. Highly diverse marine life sustains a range of fishing operations, from small- and large-scale artisanal to industrial fisheries (Isaac et al. 2009).

    Ethical considerations

    Our research follows the Resolution nº 466, of 12 December 2012 by the Brazilian National Health Council Plenary, which provides guidelines and norms regulating research involving human beings, and the European Commission’s directives on ethics in Social Science and Humanities (European Commission 2021).

    Fisheries landings in Bragança and challenges to governance

    As per the most recent available official national statistics on marine capture fisheries in Brazil, the state of Pará ranks second in the country in terms of fisheries production with 153,332.3 tonnes landed in 2011 (MPA 2011). Marine fisheries in North Brazil are highly diverse, multispecies and multi-gear. Isaac et al. (2009) identified 20 fishery production systems within 3 fishery types: small-scale artisanal fisheries, large-scale artisanal or semi-industrial, and industrial fisheries. Small-scale fisheries use small wooden boats of less than 12 meters in length and have a relatively low environmental impact (in terms of, e.g., exploitation status of targeted stock, level of discards) while mostly contributing to local diets and livelihoods. Large-scale fisheries operate wooden vessels between 12 and 15 meters, while industrial fisheries use steel boats and have a higher environmental impact (Isaac et al. 2009).

    Figure 2 shows some of the main organizations in charge of developing and implementing fisheries regulations at different governance levels in our study region, the coastal municipality of Bragança, Pará. Fisheries governance in Brazil is de jure decentralized, i.e., regional and local institutions are delegated power and management by the central governments (Glaser and Gorris 2023). Key legal frameworks have been developed since re-democratization in Brazil (for a federal-level analysis of key legal frameworks for fisheries governance see Nakamura and Hazin 2020; for the Pará state-level, see Alencar et al. 2022). The National Policy for the Sustainable Development of Traditional Peoples and Communities (Decree no. 6040/2007) recognizes the social and political rights of traditional populations, including access to terrestrial and aquatic territories. The National Policy for the Sustainable Development of Aquaculture and Fisheries (Law no. 11,959/2009) replaced the Fisheries Code (Decree-Law no. 221/1967) and shifted the focus from industrialization to environmental, economic, and social sustainability. These policies highlight the significance of inclusive participation, capacity building, and sustainable livelihoods in fisheries, establishing themselves as essential legal tools that influence access to fish and fisheries in Brazil.

    In the context of participation in formal governance processes, extractive reserves (RESEX; reservas extrativistas) are key institutional arrangements (Seixas and Kalikoski 2009). Extractive reserves are protected areas that aim to both secure local livelihoods and the traditional use of natural resources while integrating local populations into national development (Glaser and Da Silva Oliveira 2004). Extractive reserves are managed by a deliberative council, a multi-stakeholder body chaired by the Instituto Chico Mendes de Conservação da Biodiversidade (ICMBio). Our study area includes the Caeté-Taperaçú marine RESEX (Fig. 1), established in 2005. As per the last available statistics, the Caeté-Taperaçú marine RESEX supports approximately 8000 families who rely on its natural resources for sustenance (ICMBio 2011, https://www.gov.br/icmbio/pt-br/assuntos/noticias/ultimas-noticias/resex-marinha-de-caete-taperacu-fortalece-as-instancias-participativas) with crab (Ucides cordatus) fisheries representing the most significant economic sector (Partelow et al. 2018). Its deliberative council includes ICMBio in the lead and, among others, representatives of the users’ association Associação dos Usuários da Reserva Extrativista Marinha Caeté-Taperaçú (ASSUREMACATA, hereafter users’ association), the Z-17 Fishers’ Guild (Colônia de Pescadores de Bragança Z-17, hereafter the fishers’ guild), and the Artisanal Fishers’ Union of Bragança (Sindicato dos Pescadores Artesanais de Bragança, hereafter the fishers’ union; federal ordinance no. 17, of 24 September 2007). Although the RESEX are designed to enhance participatory governance, limited engagement with its political processes has been noted (Partelow et al. 2018). This is often linked to perceptions of procedural burdens, the marginalization of local voices, including those of younger generations in decision making, and ongoing internal power disputes (Partelow et al. 2018).

    Further institutional arrangements that promote participation at the state and local levels are the fishing agreements and the standing management committees (Comitês Permanentes de Gestão). Fishing agreements are established by local communities that formulate rules for fishing in a particular body of water, such as gear restrictions or seasonal fishing schedules. Relevant to the study area is the Caeté River Fisheries Agreement (but focused on freshwater fisheries; established through State-level SEMAS Ordinance n°1.358 of 07/2023). Standing management committees, such as the Standing Committee on Fisheries Management and the Sustainable Use of Demersal Fisheries Resources in the northern and northeast regions (established through Interministerial Ordinance n°8 of 09/2015) are consultative advisory multi-stakeholder bodies that inform decisions taken by the relevant federal authorities on given fisheries, including large-scale, artisanal, and industrial fisheries.

    Despite these arrangements, fisheries regulations still often originate at the federal level, limiting the autonomy of regional and local institutions. Power imbalances at multiple levels hinder equitable actor participation and the integration of different types of knowledge. Lack of financial and human resources, as well as data, result in less accountable local organizations (Moura et al. 2009, Wever et al. 2012, Oviedo and Bursztyn 2017). In Bragança, sustainable fisheries with a balanced and effective participation in decision making are not yet a reality (Isaac et al. 2009, Partelow et al. 2018, Borges et al. 2021). Lack of communication among stakeholders, power imbalances, and political misrepresentation are among the factors that hinder participatory engagement in fisheries management (Isaac et al. 2010, Seixas et al. 2019).

    Data collection

    This research aligns with the premises of qualitative research (Maxwell 2008). We build on a social constructivist and critical approach to acknowledge that realities are socially constructed and mediated by subjective experiences shaped by the broader context and environment; and to acknowledge the mediation of the researcher’s own subjectivity(ies) in building an understanding of the problem being explored (Schwandt 1994). More specifically, this study builds on an analysis of perceptions as socially and historically situated interpretations, understandings, and evaluations of environmental change and governance (Bennett 2016). As forms of situated knowledge, perceptions are shaped by political and economic structures, institutional contexts, prevailing power relations, and everyday lived experiences.

    Data were collected using a participatory network mapping method called Net-Map pioneered by and adapted from Schiffer and Hauck (2010). Net-Map allows the study and understanding of perceptions of complex governance problems (e.g., fisheries governance-related issues). A total of eight net-map interviews (Table 2) were carried out with key-informants between November 2022–March 2023 in the state of Pará, North Brazil. Net-maps #1-4 were conducted in the fishing communities of Vila do Bonifácio and Inferninho. The remaining net-maps were conducted in Bragança. Interviewees were: artisanal fishers, individuals (n = 3) or in groups (n = 2 groups of 3 fishers), and representatives of local municipal-level institutions linked to artisanal fisheries’ interests and management, namely two civil society organizations: the users’ association (n = 1) and the artisanal fishers’ union (n = 1); and one public authority, ICMBio (n = 1). Participants were selected through purposive sampling (Patton 2002) to capture a range of perspectives relating to fisheries that formally classify as artisanal, in the region of Bragança. This net-mapping approach reflects our goal of undertaking a deep qualitative exploration of the interviewees’ subjective experiences, with particular attention to their varied backgrounds and involvement in fisheries management. This allowed us to capture the complex nuances of relational power dynamics influencing access within this sector. Research fatigue observed in the region was also considered. Subsequently snowball sampling (Braun and Clarke 2013) was also used in the absence of a gatekeeper and as the lead author built a local network. In meaningfully selecting our interviewees, we aimed to explore if and how diverse targeted fish species, gear type, and thus engagement in different temporal and spatial relations within their fishing activities, influenced fishers’ perceptions. Selection criteria additionally included fishing experience for fishers’ interviewees (net-maps #1–5) and considerations of leadership within the community or relevant institutions for other participants (net-map 1; net-maps #6–8). The Z-17 fisher’s guild in Bragança is another key institution, however, requests for a net-map interview were unsuccessful. We acknowledge this limitation and recognize its impact on the scope and depth of our analysis of governance and local power dynamics.

    A first set of net-maps was conducted with individual participants (net-maps #1–3). For net-maps #4–5, a focus group approach was adopted to gather perspectives from otherwise geographically dispersed participants to encourage dynamism and reduce potential research fatigue from a time-consuming activity, and to provide insights into the ways in which accounts of governance processes are negotiated among participants (Braun and Clarke 2013). When fishers shared similarities in terms of fishery operation and community affiliation, as in net-map #4, participation was balanced. The participants in net-map #5 were involved in the municipal education system for fishers in the town of Bragança. However, they worked in different fisheries and did not share community membership. In this case, one of the participants with closer ties to formal fisheries management organizations had a more prominent voice, and care was taken to avoid over-representation. Our subsequent analysis was also informed by observations of these group power dynamics (Farnsworth and Boon 2010). The overall number of interviews is consistent with our aim of exploring a range of stakeholder-specific perceptions in depth, in accordance with the principles of qualitative research. Other studies using the Net-Map method have conducted similar numbers of interviews (e.g., N = 6 in Glaser et al. 2018).

    Before the network mapping exercises, all participants were informed of ethical considerations of the study and gave consent for the recording of their interviews. The net-map activity consisted of three steps (adapted from Schiffer and Hauck 2010):

    1. To kick-off the activity, participants were asked “Who affects and who is affected by what happens with fisheries landing in Bragança?” (based on Glaser et al. 2018). Participants mentioned different groups of people or institutions. The interviewee wrote the names on color-coded post-it notes (Table 3). Fisheries sectors were attributed different colors, depending on how participants distinguished or named them. The post-it notes were placed on a large piece of white paper. We acknowledge the epistemological and ethical implications of framing this question in a way that polarizes groups of actors into those with power and those without. Drawing on theories of power dynamics and in particular Ribot and Peluso (2003) and Peluso and Ribot (2020), we understand power as a relational force mediated by structures in which fluid hierarchies as well as everyday acts of resistance challenge static notions of power.
    2. When it was agreed that all relevant actors had been identified, participants were asked how the entities interact with each other, i.e., what types of links connect different entities. Five types of links were previously established based on Schiffer and Hauck (2010) and Glaser et al. (2018): (1) communication, (2) support/capacity building, (3) money flow, (4) control, and (5) complaint (Table 4). These links were to be represented by drawing uni- or bi-directional arrows of different colors for each type of link.
    3. As the activity proceeded, the interviewer summarized what they were seeing in terms of net-map actors and links to ensure a correct understanding of the overall picture and to prompt further explanations when needed by participants.

    Presidential elections were held in Brazil in October 2022, and a new government took office in January 2023. All net-maps produced before March 2023 are representative of the governance situation under the previous government because the configuration of ministries and secretariats under the new administration was uncertain during that time.

    Data analysis

    For this research, we used an inductive methodological approach. The net-map interviews yielded two types of outputs: (1) a visual representation of the perceived network; and (2) the interview recording. We first analyzed the net-maps produced in terms of their composition of actors and links. We then undertook a qualitative analysis of the interviews to understand how the interactions between different actors relate to access for fishing.

    Analysis of perceived networks

    Visual and basic quantitative analysis of the net-maps provided information on the network composition, i.e., on which actors were perceived by respondents, through which interactions they were related, and the respective frequencies of occurrence (based on Gerhardinger et al. 2022).

    First, the perceived networks were visually represented using the open-source software Gephi (product version 0.10.1) for network visualization. Labels were established for each actor group mentioned by the interviewee that best reflected the names originally assigned. The parameters by which participants grouped certain fisheries were discussed to assign a fishery category. The names of target fish species mentioned in common Portuguese language during the interviews were associated with scientific names based on Isaac et al. (2008) for artisanal fisheries and Frédou et al. (2008) for industrial fisheries.

    The numbers of actors and links were counted for each net-map to align with the previously established typologies. A Sankey diagram was plotted using the open-source data visualization platform RAWGraphs (Mauri et al. 2017) to represent the interactions between actors as senders and receivers, respectively, for all eight net-maps combined. To understand stakeholder specific differences of perceptions, the networks were also compared in terms of network composition.

    Qualitative analysis of interviews

    A qualitative analysis of the net-map interviews was carried out to elucidate the perceived interactions related to access to fish and fisheries. The transcripts of the interviews were initially generated using the online transcription software Sonix Inc. and were subsequently manually corrected and edited. We then conducted a thematic analysis (TA) using a deductive-inductive codebook approach based on Miles and Huberman (1994). Coding was done in the original language of the interviews, Brazilian Portuguese, using the software MaxQDA Plus version 2020. The coding process is detailed in Appendix 1. Different access issues were identified for each category of actors concerned (based on Ribot and Peluso 2003). The coding process was performed by the lead author (LD) and subsequently discussed and checked with co-authors MG and RS. The influence of the author’s subjectivity in the coding process is acknowledged.

    The results of the qualitative analysis are presented in the form of tables, which include the three most cited mechanisms of access to fish resources and fisheries for the most cited SSF, public authorities, vessel owners and post-harvest, and civil society organizations, along with the corresponding themes. The frequencies are shown per aggregate of fishers’ net-maps (net-maps #1–4), civil society organizations’ net-map #6 and net-map #7, and public authorities’ net-map #8 to better capture differences in participant groups’ perceptions.

    RESULTS

    Network map analysis: general overview

    The eight net-maps are pictured in Appendix 2. A total of 174 actors and 402 links were mentioned by participants. Small-scale fisheries (SSF) actors were the most cited actor group (n = 42), followed by public authorities (n = 36), and civil society organizations and large-scale fisheries, which were each cited 24 times (Table 5). The group of vessel owners and post-harvest actors included intermediaries, vessel owners, and the fishing and processing industries, as well as the national and international export markets.

    In fishers’ net-maps #1–5, the most frequently mentioned link type through which access is negotiated was “money flow” (n = 59), followed by “complaints” (n = 48), and “support” (n = 48; Table 5). However, in the summary net-map, SSF access through “communication” was mainly within SSF’s own group (Fig. 3). “Complaint” was the next largest link through which access to fish and fisheries was negotiated mainly among SSF. Few links were perceived coming from groups of fishers to government agencies, civil society organizations, and vessel owners and post-harvest actors. For net-map #5, whose participants work in what they classified as industrial fisheries, access was negotiated through complaint links that come from all industrial fisheries explicitly to vessel owners.

    Civil society organizations were perceived to influence SSF access mostly through support links, as in net-map #2 (Table 5). In the other fishers’ net-maps, the fishers’ guild and the artisanal fishers’ union were either absent (e.g., net-map #4) or connected through money flow to fishing actors (as a mandatory contribution for membership) as in net-map #3. The fishers’ guild and the artisanal fishers’ union were poorly connected to each other and to SSF from the fishers’ perspective. In both civil society organizations’ net-maps (net-map #7–8), the RESEX users’ association facilitated access of fishing actors through “control,” “communication,” and “support.” The artisanal fishers’ union, on the other hand, appeared only in its own net-map, with no link to fishing actors, and appeared to play a minor role in facilitating fishers’ access. Contrary to fishers’ perceptions, civil society organizations’ respondents saw SSF actors with limited links to each other.

    In contrast to the low mentions of interactions emanating from SSF to public authorities, SSF received around half (n = 38) of the total links coming from public authorities (n = 74), which translated a strong overall perception of influence of the latter over SSF. Public authorities mostly regulated access of SSF through control (net-map #3–6, Table 5). The government representative interviewed was the only respondent to depict a systematic bi-directional communication network between the government agency represented (ICMBio) and all fisheries actors. No direct connection between ICMBio and the RESEX users’ association was mentioned by the public authority respondent. No complaints were perceived among or between formal organizations, but all fisheries were mentioned to have complaints among themselves. Despite receiving very few links coming from other actors, vessel owners and post-harvest actors largely controlled SSF and large-scale artisanal fisheries’ access through money flow.

    Qualitative analysis of interviews

    Knowledge, technology, and legal-based mechanisms were particularly relevant for SSF access. Figure 4 shows the average number of mentions per interview aggregate (net-maps #1–4; net-map #6; and net-maps #7–8) relating to different mechanisms of access. Small-scale fisheries’ access to fish was mostly linked to knowledge of the biogeophysical environment and in particular to the characteristics of the target species, as illustrated by the following quote:

    This is the time for net fishing when the moon is full. That’s the time to net the pescada-amarela [Cynoscion acoupa], which is the best. (net-map#2)

    The second most cited dimension of access was technology. Small-scale fisheries’ reliance on technology to adapt to changes in fish behavior and environmental conditions becomes particularly evident when access to this technology is restricted:

    [...] if we had another type of material net, then we’d go somewhere else, right? Antônio [...] has 400 meters of fishing nets. Then his fishing won’t stop, because he’s already got the pescada [Cynoscion acoupa], he’s got the corvina [Cynoscion virescens], he’s got the uritinga [Sciades proops], he can fish and keep his pattern up all the time, right? (net-map #4)

    Technology was also a topic in many of the complaint links among SSF that related to gear conflicts and aspects of everyday negotiations for access to fish and fisheries. Legal-based mechanisms represented challenges to SSF access. Small-scale fisheries struggle to obtain official documentation confirming their formal status as fishers, which impedes their ability to advocate for their rights and engage in disputes with industrial fishers.

    Technology and markets were important for both large-scale artisanal- and industrial fisheries. Public authorities were perceived to control SSF access through legal mechanisms, knowledge, and illegal mechanisms. In terms of access through legal mechanisms, public authorities were mostly perceived to fail to facilitate fishers’ access (access obstruction) or to exercise unfairly differentiated legally based authority over SSF:

    Why don’t they go to the industrial boats, which damage a lot more? They don’t control them. Because they want to control us, because it’s easy to control the small ones, it's very easy. (net-map #2)

    Civil society organizations were importantly related to the exercise of control through legal mechanisms, social identity, and knowledge. Civil society organizations were perceived as often obstructing access through legal-based mechanisms, as highlighted by this interviewee:

    We paid the colony [fishers’ guild] with all our heart. I’m fishing. I can't work [because of health issues] for two, five months, a year. It should pay an aid to the person, you know? And it never did that. (net-map #1)

    Obstructed access often translated into complaint links in the net-maps. Vessel owners and post-harvest actors were frequently considered as mediating access to markets and capital. Appendix 3 provides quotes to illustrate further access mechanisms that are at the root of the more frequently occurring codes for SSF, public authorities, vessel owners and post-harvest actors, and civil society organizations.

    DISCUSSION

    Navigating access: social organization among fishers

    Communication links between SSF mostly convey information about everyday fishing praxis and knowledge. Knowledge was the most frequently mentioned access mechanism for SSF, in line with Andriamahefazafy and Kull’s (2019) findings. Local fishing knowledge (LFK) refers to the understanding, meanings, and constructs associated with the environment and human-nature feedback, importantly allowing for the adaptation of fishing strategies and improved access to fishing resources. Our coding reveals that LFK contains elaborate details on the dynamics of fish migration, feeding and reproduction habits, and on how these habits are influenced by environmental factors. Our findings are in line with Barboza and Pezzutti (2011) who highlighted the richness of LFK and terminologies used by fishers from one of our study sites, Vila do Bonifácio. The terminologies and beliefs relating to the workings of nature (e.g., as the work of God and/or as a twist of fate) revealed by our interviews testify to the continuous (re)construction of imaginaries of coastal entanglement and thus influence how access is permanently (re)negotiated at the individual subjective and collective levels. Despite the absence of formal institutions to support and regulate artisanal fisheries perceived by our interviewees and reported in other Amazonian fishery contexts (Maneschy 1990, Doria et al. 2021, Alencar et al. 2022), the abundance of ties among SSF is thus evidence of informal social networks in artisanal fisheries and merits investigation into the implications for social organization in fisheries. The fact that conflicts internal to SSF were frequently cited by non-fisher interviewees may be due to an apparent propensity to mention conflicts elsewhere but not those respondents themselves were involved in. For instance, civil society organizations’ representatives and public authorities involved in fisheries management may tend to highlight the existence of fisheries conflicts to legitimize their authority to control access (Peluso and Ribot 2020). Government agencies at multiple levels play a pivotal role in the management of fisheries conflicts and have the capacity to promote positive social transformation (SSF guidelines, FAO 2015, Dahlet et al. 2021). However, in contexts such as Bragança, where government infrastructure for artisanal fisheries is weak, local communities may be compelled to foster their own institutions for conflict resolution, as observed in other parts of Brazil (Prado et al. 2021) and in tropical fisheries more broadly (Dahlet et al. 2021).

    Public authorities: controlling, unreachable, or missing

    The relatively few links that come from SSF and go to public authorities (n = 6) suggest limited power or influence of the former over the latter, and a shared perception that public authorities are not accessible. In essence, control links are understood as activities of inspection (fiscalização), which is perceived as the pinnacle of government authority. This control enforces formal regulations for particular fisheries, restricting short-term access to fish with the promise of protecting fish stocks, ultimately securing long-term access for fishers. This generated livelihood and equity issues. We concur with Fabinyi et al. (2015) that, beyond concerns over the ecological health of fish stocks, equity impacts of control activities are central for SSF. In the Bragança region, the lack of inspection activities was on the one hand seen to illustrate the government’s absence and neglect of artisanal fisheries. On the other hand, the regulatory authorities responsible for inspection (e.g., IBAMA) were criticized for conducting excessive inspections of small-scale fishers, who are more deprived of capital and material resources, while failing to monitor the most powerful groups of fishers, such as industrial trawlers, despite their involvement in the most destructive fishing practices. A similar “command-and-control” approach adopted by ICMBio and IBAMA is perceived by coastal users in the Tamandaré region in Northeast Brazil (Glaser et al. 2018). Our results reveal that inspection is seen to have an ambivalent role. Subject to inspection by state authorities, the “inspected” become a political subject. But when inspection is disproportionately focused on the most vulnerable groups, it becomes a matter of discrimination underpinned by important power imbalances. The Brazilian Navy seems to have greater legitimacy among SSF because it provides capacity-building activities that are mandatory for the acquisition of a fishing license. Although not formally responsible for fisheries management, the Brazilian Navy appears to play a gatekeeping role in the bureaucratic process of fisher formalization. This process directly affects SSF access to licenses, and by extension, to fishing rights.

    Our findings also indicate perceptions of further forms of marginalization under the code of “access denied/obstructed,” echoing Hall et. al.’s (2011) notion of powers of exclusion, cited in Myers and Hansen (2019). For instance, unlike industrial fishers, who typically have better administrative support and formalized documentation, artisanal fishers often struggle to obtain the General Register of Fishing Activity (Registro Geral da Atividade Pesqueira, RGP), the official document issued by the Ministry of Fisheries and Aquaculture that certifies their profession. The RGP is essential not only for legal recognition but also for accessing social protection and other public policies in support of artisanal fisheries. Getting the official documents is challenging for several reasons, including difficult access to public authorities and corruption or inaction by civil society organizations. Efforts to remedy this situation at the federal level include the creation of the National Secretariat for Registration, Monitoring and Research within the Ministry of Fisheries and Aquaculture, and at the Bragança level within the Municipal Secretariat for Fisheries and Aquaculture. In this context, our findings suggest that civil society organizations such as the fishers’ guild and the artisanal fishers’ union are held responsible for supporting and providing their members with access to legal mechanisms.

    Civil society organizations and challenges to fishers’ representation

    The fishers’ guild and artisanal fishers’ union are perceived to be institutions for safeguarding fishers’ rights, including access to social security benefits like pensions and benefits in times of unemployment and ill-health. Fishing is a highly risky and physically demanding activity (Sales et al. 2022) and access to health benefits is essential. The lack of trust and perceived inefficacy of artisanal fishers toward these organizations, and in particular the fishers’ guild, may explain the low membership rate of 48% of registered fishers in Pará (Lourenço et al. 2006). Fishers’ guilds in Brazil were first established by the Brazilian Navy in the 1920s, undermining the autonomy of fishing communities (Ramalho 2014). In other parts of the world where fishers’ guilds have emerged in a bottom-up fashion, they are now actively involved in local environmental management (e.g., in Spain, see Herrera-Racionero et al. 2022). In this sense, future research appears needed to examine and situate the role of fishers’ guilds and unions as pivotal actors within the Brazilian decentralized governance system, as well as their potential and actual influence on context-specific collective action.

    In contrast, the RESEX Caeté-Taperaçú emerged from grassroots efforts supported by public authorities, social movements, and academia (do Nascimento 2021). The users’ association’s representative speaks of the organization as belonging to the people and claims to represent SSF against abuses by banks, intermediaries, and the fishing industry, among others. This is reflected in the number of mentions that related civil society organizations to social identity in the qualitative analysis of net-map #8. Because the RESEX Caeté-Taperaçú is not mentioned at all in three of the five fishers’ maps, perceptions of its influence on fisheries governance are diverse. Social identity is key for improved SSF access (e.g., Bennett et al. 2021). In Bragança and other locations where large-scale fisheries and/or tourism are absorbing the labor of small-scale fishers, ecosystems are becoming increasingly degraded, and fishing livelihoods and related social identities are undermined. This, in turn, may affect the capacities for collective action by fishers and increase their dependence on government intervention (Ramalho 2014, Pinkerton 2019).

    Partelow et al. (2018) found that the RESEX Caeté-Taperaçú has been increasingly seen as a government social aid program facilitating access to housing and material goods rather than an institution actively embodying the collective management of natural resources. Our interviews confirmed this. The users’ association is linked to the National Program for Agrarian Reform and gives access to its members to programs and public policies such as the Bolsa Verde (green allowance) or agrarian reform credits, which are key among the few forms of public support available to the poor, remote communities within the RESEX (Prado and Seixas 2018).

    Improving the formalization of SSF is a key FAO recommendation to nation states as a means of securing access to those working within these fisheries (FAO 2022). This could be achieved through the development of a legal framework for community-based resource management (Mertens et al. 2015, Blythe et al. 2017), in which artisanal fishers have formalized rights to manage their fisheries, and this extends beyond Caeté-Taperaçú marine RESEX boundaries (Borges et al. 2021). Articulating such a framework with the institutions linked to the RESEX may be challenging. Environmental NGOs active in the region have played an important role in supporting community organization and co-management efforts (Rare Brasil 2021). Social movements emerge as relevant enablers for scaling up SSF struggles to other levels of governance and improving local leadership capacity and conservation outcomes (Potiguar Júnior 2007, Pinkerton 2017). That no such NGOs and movements were mentioned by fisher respondents indicates a need for local outreach and mobilization.

    Vessel owners and post-harvest actors filling the governance gap through capital and market

    The predominance of money flow links from vessel owners and post-harvest actors to SSFs suggests a one-way influence in which the former control artisanal fishers’ access to markets and capital. On the Pará coast, artisanal fisheries typically rely on the marreteiro (middleman) to handle smaller quantities of fish and local markets and villages, while the intermediário (intermediary) handles larger production volumes and may resell to the national and international market. Both types of traders may also act as vessel owner, fishing gear financier, and/or moneylender including when catches are low, when illness prevents fishing, or when fishers suffer financial distress. Most of these transactions take place informally. Small-scale fisheries reliance on the marreteiro and intermediário will thus likely increase as public authorities and civil society organizations, such as the fishers’ guild, fail to provide effective legal support. Research by Poissant et al. (2023) in the rural Peruvian Amazon suggested that geographic isolation increases dependency of SSF on powerful intermediary actors. Similarly, Basurto et al. (2013) linked isolation to less cooperative behaviors and greater reliance on intermediaries. In our study area, the road construction in the 1970s cutting through the mangroves swamp provided a faster access route linking the coastal communities of Vila do Bonifácio and Vila dos Pescadores to the urban center of Bragança. This provoked a surge in intermediários (Oliveira and Henrique 2018). Coupled with limited traditions of collective action, the prevalence of informality in the SSF value chain, also appears to intensify the dependency of SSF on intermediários, which may potentially lead to increased exploitation of fishers, increased fishing pressure and a reduction in fish availability (Miñarro et al. 2016, Poissant et al. 2023).

    Access to technology and capital remains a major barrier to SSF access in Bragança, a challenge also identified in other regions of Brazil (Haque et al. 2015). In an effort to improve access to credit, the Brazilian government introduced the Plano Safra da Agricultura Familiar in June 2023, which provides loans for SSF. Access to these loans is prevented, however, by difficult bureaucracy, poor repayment terms and rates, and fear of losing assets (Haque et al. 2015). As a result, fishers in Bragança often turn to their informal social networks, which include their intermediaries, for support. Another layer of complexity is added when the marreteiro or intermediário is the respective fisher’s relative such as in the case of the interviewee in net-map #2 whose uncle is the vessel owner and whose cousin is the marreteiro. Kinship networks play a central role in controlling and maintaining access to resources in Amazonia (Alencar et al. 2014), including in the context of erosion and resource depletion, as seen in Inferninho and Vila do Bonifácio. Characteristics of patron-client relationships were mentioned by our interviewees, but few complaint links came from SSF to intermediaries. This may indicate the ambiguity inherent in such relationships. Only net-map #5 discloses systematic complaint links flowing from all industrial fisheries to boat owners who are also fish traders indicating that the importance of informal and kinship links is a special feature of SSF in our research region.

    CONCLUSION

    This study explores how coastal and marine fisheries governance networks are seen to affect artisanal fishers’ access in Bragança, on the northeast Amazonian coast of Brazil, from the perspectives of a number of different relevant actors.

    Fishers in both small-scale artisanal and large-scale artisanal fisheries are perceived to negotiate access to fish and fisheries among themselves, mostly on a daily basis, through communication and complaint links. These interactions are related to knowledge (e.g., communicating knowledge of the biogeophysical environment) and technology (e.g., gear conflicts). Public authorities and civil society organizations are seen to control fishers’ access through legally based mechanisms. However, these actors are portrayed as absent (e.g., obstructing access), unreachable, or lacking in reliability and fairness. When connected to SSF, public authorities are mostly reported to exert restrictive control of SSF through diverse means. Artisanal fishers lack a robust representation. Respondents perceived respective institutions, i.e., the fishers’ guild and the artisanal fishers’ union as failing to fulfil their main function: facilitating access to vital benefits of public policies (e.g., access through legally based mechanisms). Similarly, and despite a contrasting early history (Glaser et al. 2010), the influence of the association of the Caeté-Taperaçú extractive reserve appears to be limited now. In the absence of support from public authorities and civil society organizations, actors linked to vessel owners and the post-harvest sector are asserting their influence by controlling fishers’ access to markets and capital. In these relationships, SSF frequently find themselves depending on intermediaries for loans, or even narcotics, which must then be repaid with lower prices received for their catches.

    Fisheries governance in Bragança is based more on market mechanisms and unequal forms of dependency (Johnson 2010) than on supportive laws drawn up by the public authorities. The results of our research draw attention to the need to: (1) enhance accessibility to public policies and government programs to strengthen the formalization of artisanal fisheries, taking into account its local characteristics and particularities, including the social organization already in place among artisanal fishers; (2) mobilize financial and human resources for local public authorities geared to improving access and equitable participation of artisanal fishers in decision-making forums; (3) facilitate access to the market and capital for artisanal fishers, for example, by incentivizing the establishment of a cooperative or other forms of innovation; (4) promote and encourage artisanal fishers’ organization and representation, for instance, by facilitating funding for capacity development in local leadership. These measures can only be fully effective if the need for basic education and health service structures is also addressed. The work presented here shows that promoting more equitable access for, and encouraging dialogue with, artisanal fishers are essential and missing prerequisites for sustainable development in the Amazon.

    The integration of net mapping and access analysis provides valuable insights for the development of more inclusive marine conservation policies. Future research could examine how perceived governance networks evolve in response to significant institutional and environmental shifts, such as the proposed designation of a protected area vis-à-vis competing plans for oil exploitation in the Brazilian Amazon Shelf (Araujo et al. 2021). Longitudinal and multi-scalar analyses could shed light on how climate change compounds access challenges for artisanal fishers and how governance dynamics vary across levels. Additionally, further attention to the influence of non-state actors and the role of gender and intersecting power relations in shaping network influence remains crucial.

    This becomes even more critical as aquaculture and oil exploration interests grow in the Amazon estuary, and in view of the upcoming 30th Conference of the Parties to the United Nations Framework Convention on Climate Change (UNFCCC COP 30) to be held in Belém in November 2025.

    RESPONSES TO THIS ARTICLE

    Responses to this article are invited. If accepted for publication, your response will be hyperlinked to the article. To submit a response, follow this link. To read responses already accepted, follow this link.

    AUTHOR CONTRIBUTIONS

    Lol Dahlet: conceptualization, methodology, investigation, formal analysis, data curation, validation, writing – original draft, writing – review & editing, visualization, funding acquisition. Roberta S. L. Barboza: supervision, conceptualization, validation, writing – review & editing. Ingrid van Putten: validation, writing - review & editing. Aniekan Akpan: data curation. Rapti S. de-Zoysa: writing - review & editing. Marion Glaser: supervision, conceptualization, methodology, investigation, validation, funding acquisition, writing – review & editing.

    ACKNOWLEDGMENTS

    We express our sincere gratitude to all those who made this research possible, in particular the interviewees in Bragança who generously gave their time and shared their knowledge and experience. Special thanks are due to Victoria Isaac and Bianca Bentes for insightful discussions at an early stage of this research. We also thank Sr. Antônio Melo, Sr. Danilo Gardunho, and Sr. João Farias for their generous support and guidance throughout the research process. We are grateful to the three anonymous reviewers for their constructive comments and suggestions, which greatly helped to improve this manuscript. LD is grateful to CAPES/DAAD for the full PhD fellowship awarded. We also acknowledge the NoCRISES project, which is funded by the Federal Ministry of Education and Research (BMBF, 03F0845A), the Leibniz Centre for Tropical Marine Research (ZMT), the BremenIDEA funding line of the University of Bremen, and the Laboratório de Ensino, Pesquisa e Extensão Pesqueira junto a Comunidades Amazônicas (LABPEXCA) of the Universidade Federal do Pará (UFPA, Bragança campus). These organizations provided the essential resources and framework that enabled this research. The present research received the ethical approval of the Brazilian National Research Ethics Committee (CONEP; Plataforma Brasil, CAAE: 65040122.3.0000.0018) and the ICMBio SISBIO authorization to conduct research within Federal Conservation Units (SISBIO license no. 82744-1).

    Use of Artificial Intelligence (AI) and AI-assisted Tools

    We acknowledge the use of DeepL Translate [DeepL.com] to generate translations from Brazilian Portuguese into English in the process of writing this article.

    DATA AVAILABILITY

    The data and code that support the findings of this study are available on request from the corresponding author, LD, and subject to privacy/ethical restrictions. None of the data and code are publicly available because they contain information that could compromise the privacy of research participants. Ethical approval for this research was granted by the Brazilian National Research Ethics Committee (CONEP) (Plataforma Brasil, CAAE: 65040122.3.0000.0018) and through the ICMBio SISBIO authorization to conduct research within Federal Conservation Units (SISBIO license no. 82744-1).

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    Corresponding author:
    Lol Dahlet
    lol.dahlet@leibniz-zmt.de
    Appendix 1
    Appendix 2
    Appendix 3
    Fig. 1
    Fig. 1. Map of the study area. <sup>†</sup> Two marine extractive reserves (RESEX) lie within the municipality of Bragança: the Tracuateua marine RESEX to the west and the Caeté-Taperaçú marine RESEX to the east. The latter is central to this study because it is where data were collected. The boundaries corresponding to the RESEX of Cuinarana and Filhos do Mangue are not included in the map. The corresponding data were last updated in 2022, before both RESEX were officially decreed in March 2024.

    Fig. 1. Map of the study area. † Two marine extractive reserves (RESEX) lie within the municipality of Bragança: the Tracuateua marine RESEX to the west and the Caeté-Taperaçú marine RESEX to the east. The latter is central to this study because it is where data were collected. The boundaries corresponding to the RESEX of Cuinarana and Filhos do Mangue are not included in the map. The corresponding data were last updated in 2022, before both RESEX were officially decreed in March 2024.

    Fig. 1
    Fig. 2
    Fig. 2. Selected relevant organizations involved in fisheries governance in Bragança, Pará, Brazil, as identified during the research process (non-exhaustive).

    Fig. 2. Selected relevant organizations involved in fisheries governance in Bragança, Pará, Brazil, as identified during the research process (non-exhaustive).

    Fig. 2
    Fig. 3
    Fig. 3. Absolute frequency and directionality of links and link types by actor group (N = 402 links). The height of each rectangle reflects how often a given link type was identified. The colors of the flows on the left represent different actor groups (sources of the links), and the colors on the right represent different interaction types (link types).

    Fig. 3. Absolute frequency and directionality of links and link types by actor group (N = 402 links). The height of each rectangle reflects how often a given link type was identified. The colors of the flows on the left represent different actor groups (sources of the links), and the colors on the right represent different interaction types (link types).

    Fig. 3
    Fig. 4
    Fig. 4. Heatmaps showing the mean frequency of text units coded relating to different mechanisms of access (x-axis) and groups of actors (y-axis) by net-maps aggregates: (A) artisanal fishers’ net-maps taken together (n = 4); (B) the public authority representatives (n = 1); and (C) civil society representatives’ net-maps taken together (n = 2). SSF = small-scale fisheries; LSF = large-scale fisheries; IF = industrial fisheries; VOPH = vessel owners and post-harvest; PA = public authorities; CSO = civil society organizations; REO = research and education organizations; BUS = other businesses; MSB = multi-stakeholder bodies.

    Fig. 4. Heatmaps showing the mean frequency of text units coded relating to different mechanisms of access (x-axis) and groups of actors (y-axis) by net-maps aggregates: (A) artisanal fishers’ net-maps taken together (n = 4); (B) the public authority representatives (n = 1); and (C) civil society representatives’ net-maps taken together (n = 2). SSF = small-scale fisheries; LSF = large-scale fisheries; IF = industrial fisheries; VOPH = vessel owners and post-harvest; PA = public authorities; CSO = civil society organizations; REO = research and education organizations; BUS = other businesses; MSB = multi-stakeholder bodies.

    Fig. 4
    Table 1
    Table 1. Description of the different mechanisms of access after Ribot and Peluso (2003).

    Table 1. Description of the different mechanisms of access after Ribot and Peluso (2003).

    Access mechanism Explanation
    Structural and relational mechanisms
     Technology Refers to the need for fishing gear (including vessels) and other equipment that may favor access to particular fish species and fisheries.
     Capital In terms of wealth, access to capital allows, for example, the acquisition of fishing gear and other technological equipment, as well as the mobilization of labor.
     Markets Access to markets refers to the ability to benefit commercially from fish and fisheries. Markets can be defined at local, national, and/or international levels, and the struggle for access to certain markets (e.g., setting prices) can be linked to exclusionary practices.
     Labor and labor opportunities Labor and labor opportunities are key elements of access to different fish and fisheries. They also define the distribution of benefits because those who control labor opportunities can define the conditions of work relations (including in terms of contract formalization and remuneration scheme).
     Knowledge Knowledge affects who has access and how. For example, access to a particular fishery requires knowledge of the biogeophysical environment as well as the technology required. Knowledge systems also include beliefs and discursive practices that shape meaning making. The ability to access and control information and what knowledge counts in decision making is often linked to issues of power.
     Authority Authority is generally associated with a concentration of power over and control of access. For example, formal and informal organizations need authority to develop and enforce legitimate access rules. Less authoritative groups may be more subject to coercion and thus restrictive control over their activities.
     Social identity Social identity influences access on several levels and is relevant to all other dimensions of access. At the local level, it may influence the sharing of knowledge, aspects such as authority or prejudice and exclusion, as well as allocation of benefits from public policies.
     Negotiation of other social relations Although all other dimensions of access are also forms of social relations, this particular type of mechanism refers to the array of relationships such as trust, friendship, conflict, and dependency as means of negotiating access. Structural, political, and economic changes can alter context-specific social networks of access.
    Rights-based mechanisms
     Legal-based Legal access is mediated by formal and informal laws, regulations, and conventions. In fisheries, fishers often need a fishing licence from the relevant government agency to be formally allowed to fish and to benefit from government programs that support fishing-dependent livelihoods.
     Illegal-based Illegal access occurs when formal and informal access rules are violated. Typically, in fisheries, this occurs when prohibited fishing practices and gear are used to catch fish. It also includes corruption and theft combined with the use of coercive force.
    Table 2
    Table 2. Overview of Net-Map interviews between November 2022 and March 2023 in Bragança, State of Pará, Brazil.

    Table 2. Overview of Net-Map interviews between November 2022 and March 2023 in Bragança, State of Pará, Brazil.

    net-map #ID Groups of fishers and formal institutions interviewed, and fishing ground/place of work Of what sector Single-participant or focus group Age group Basic participant fishing-related information Interview duration (in minutes)
    1 Diverse fishes (net, river, and estuary) SSF Key informant 40–49 Participant only worked in small-scale artisanal fisheries, owns his own boat and gear, and goes fishing with another person, usually a relative; is familiar with the Municipal Secretariat for Fishing through a relative working there. 155
    2 Cynoscion acoupa fishery (net and longline, estuary, and coastal) SSF Key informant 20–29 Participant only worked in small-scale fisheries, owns his own boat and gear, and goes fishing with another person, usually a relative. Descends from the founders of the fishing village Vila do Bonifácio in 1913. 81
    3 Acoupa weakfish fishery (net and longline, estuary, and coastal) SSF Key informant 50–59 Participant owns his own boat and gear and goes fishing with another person, usually a relative. Has already worked in large-scale artisanal fisheries close to the international border with French Guiana. Descends from the founders of the fishing village Vila do Bonifácio in 1913. 120
    4 Diverse fishes (fixed trap (curral), estuary) SSF Focus group
    (3 participants)
    50–69 Participants live in the community of Inferninho and have close personal ties. They have always operated mainly in curral fisheries; they own their own curral, go fishing with another person, usually a relative; are leading members of the Curral Fishing Association, which is supported by the Municipal Secretariat for Fishing and are recognized as local fishing community leaders. 99
    5 Mixed fisheries (coastal shrimp, Gillbacker sea catfish, Acoupa weakfish; net and longline, coastal, and Northwards up to the international border with French Guiana) SSF and LSF Focus group
    (4 participants)
    40–59 Participants worked in both small-scale and large-scale artisanal fisheries; they may or may not own a boat and gear; go fishing with relatives and with crew in larger fishing boats; one participant working as volunteer with ICMBio. 120†
    6 ICMBio, Bragança region Public authority Key informant 40–49 At the time of the interview, the participant had been in charge of social-environmental management at ICMBio for two years and was not a fisher. 79
    7 Artisanal fishers’ union, Bragança region Civil society organization representing artisanal fishers Key informant 50–59 Participant originally came from a fishing community and is a small-scale artisanal fisherwoman. She holds a leading position in the artisanal fisher’s union in Bragança and in her community, and was exclusively dedicated to this position at the time of the interview. 124
    8 Assuremacata (Caeté-Taperaçú marine RESEX users’ association), Bragança region Civil society organization representing mostly small-scale fishers Key informant 50–59 Participant is a small-scale artisanal fisher and has a political and activist career in favor of small-scale artisanal fishing in the region. At the moment of the interview, he was exclusively dedicated to his position at the RESEX users’ association. 195
    SSF =Small-scale artisanal fisheries.
    † The recording of the interview for net-map #5 was unsuccessful and thus was not included in the qualitative data analysis of this research.
    Table 3
    Table 3. Net-Map actors’ classification and their corresponding post-it note color.

    Table 3. Net-Map actors’ classification and their corresponding post-it note color.

    Classification of actors Corresponding color
    Small-scale artisanal fisheries (SSF) Yellow
    Large-scale artisanal fisheries (LSF) Green
    Industrial fisheries (IF) Blue
    Vessel owners and post-harvest (VOPH) Orange
    Other onshore and offshore businesses (BUS) Purple
    Public authorities (PA) Pink
    Research and education organizations (REO) Gray
    Civil society and civil society organizations (CSO) White
    Table 4
    Table 4. Definition of the types of interactions used in the net-maps and the corresponding arrow color used for the graphical representation. All definitions of types of interactions were sourced and adapted from the Cambridge dictionary online.

    Table 4. Definition of the types of interactions used in the net-maps and the corresponding arrow color used for the graphical representation. All definitions of types of interactions were sourced and adapted from the Cambridge dictionary online.

    Types of links Definition Access implications Corresponding link color
    Communication Process by which a message or information is sent from one place or person to another, or the message itself Communication links are conceptualized as knowledge exchange. The exchange of information about fisheries between fishers on land or at sea improves access to fish and fisheries (e.g., Crona 2006), as does the existence of conflict resolution mechanisms when access is obstructed or contested. Blue
    Support/
    cooperation
    To encourage someone or something because you want them, or it, to succeed; the act of working together with someone Support links are conceptualized as asset sharing, capacity building, funding, and sharing of other forms of material resourcing (e.g., Partelow et al. 2018). Support is positively related to improved access. Green
    Money flow The process by which money is moved from one place or by one person to another Money flow is conceptualized as the existence of formal or informal labor contracts, selling contracts, credits, or loans. An increased access to markets, financial capital, and labor for fishers is associated with greater fish catches and access to fishing gears (Poissant et al. 2023). Yellow
    Control To order, limit, or rule something or someone’s actions or behavior Control links are conceptualized as indicative of enforcement of (formal or customary) fishing regulations. Although these may be designed to sustain fisheries in the long term, in the short term, they are likely to restrict fishers’ access to fish and fisheries. If fishers perceive that control is unevenly enforced (i.e., one group benefits from greater access) or that regulations are not legitimate (e.g., unfair restriction of access), this may result in complaints to the controlling body (see Fabinyi et al. 2015). Brown
    Complaint A statement that something is wrong or not satisfactory Complaint links are conceptualized as contestations of perceived unequitable access to fish and fisheries (Glaser et al, 2018, Saunders et al. 2024). Complaints may reflect a spectrum of conflict situations, ranging from latent to more evident. Red
    Table 5
    Table 5. Number of mentions of actor and link types for each Net-Map, following the classification approach by Schiffer and Hauck (2010) and Glaser et al. (2018). A higher number of mentions indicates that the actors or connections are perceived as the most prominent across the maps.

    Table 5. Number of mentions of actor and link types for each Net-Map, following the classification approach by Schiffer and Hauck (2010) and Glaser et al. (2018). A higher number of mentions indicates that the actors or connections are perceived as the most prominent across the maps.

    net-map #ID Number of actors mentioned Total actors Number of link types mentioned Total links
    SSF LSF IF VOPH PA CSO REO BUS MSB comm supp mon cont compl
    1 1 2 2 4 5 1 1 0 0 16 8 2 8 0 8 26
    2 5 9 3 2 4 2 0 1 0 25 12 30 17 2 18 79
    3 4 4 3 2 3 2 0 0 0 18 12 3 18 10 9 52
    4 5 2 2 2 5 2 0 0 0 18 2 9 3 5 8 27
    5 7 0 4 4 6 4 2 0 0 27 8 4 13 5 6 36
    6 5 2 2 1 6 2 1 0 1 20 38 7 4 14 17 80
    7 10 4 2 4 3 6 1 0 0 30 21 3 13 3 9 49
    8 5 1 1 3 4 3 2 1 0 20 19 9 11 4 10 53
    Total 42 24 19 22 36 22 7 2 1 174 120 67 87 43 85 402
    SSF = small-scale artisanal fisheries; LSF = large-scale artisanal fisheries; IF = industrial fisheries; VOPH = vessel owners and post-harvest; PA = public authorities; CSO = civil society organizations; REO = research and education organizations; BUS = other businesses; MSB = multi-stakeholder bodies; comm = communication; supp = cooperation/support; mon = money flow; cont = control; compl = complaint.
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    Home > VOLUME 30 > ISSUE 3 > Article 29 Research

    Capturing the multidimensionality of land-use agents in a deforestation hotspot

    Faingerch, M., T. Kuemmerle, M. Baumann, M. Texeira, and M. E. Mastrangelo. 2025. Capturing the multidimensionality of land-use agents in a deforestation hotspot. Ecology and Society 30(3):29. https://doi.org/10.5751/ES-16487-300329
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    • Melina FaingerchORCIDcontact author, Melina Faingerch
      Grupo de Estudio de Agroecosistemas y Paisajes Rurales, Facultad de Ciencias Agrarias, Universidad Nacional de Mar del Plata, Argentina; Consejo Nacional de Investigaciones Científicas y Técnicas (CONICET), Argentina
    • Tobias KuemmerleORCID, Tobias Kuemmerle
      Geography Department, Humboldt-Universität zu Berlin, Germany; Integrative Research Institute on Transformations of Human–Environment Systems (IRI THESys), Humboldt-Universität zu Berlin, Germany
    • Matthias BaumannORCID, Matthias Baumann
      Geography Department, Humboldt-Universität zu Berlin, Germany
    • Marcos TexeiraORCID, Marcos Texeira
      Departamento de Métodos Cuantitativos y Sistemas de Información, Facultad de Agronomía, Universidad de Buenos Aires, Argentina; IFEVA, Universidad de Buenos Aires, Argentina
    • Matias E. MastrangeloORCIDMatias E. Mastrangelo
      Grupo de Estudio de Agroecosistemas y Paisajes Rurales, Facultad de Ciencias Agrarias, Universidad Nacional de Mar del Plata, Argentina; Consejo Nacional de Investigaciones Científicas y Técnicas (CONICET), Argentina

    The following is the established format for referencing this article:

    Faingerch, M., T. Kuemmerle, M. Baumann, M. Texeira, and M. E. Mastrangelo. 2025. Capturing the multidimensionality of land-use agents in a deforestation hotspot. Ecology and Society 30(3):29.

    https://doi.org/10.5751/ES-16487-300329

  • Introduction
  • Methods
  • Results
  • Discussion
  • Responses to this Article
  • Author Contributions
  • Acknowledgments
  • Use of Artificial Intelligence (AI) and AI-assisted Tools
  • Data Availability
  • Literature Cited
  • commodity frontiers; deforestation; land-use actors; tropical dry woodlands and savannas; typology
    Capturing the multidimensionality of land-use agents in a deforestation hotspot
    Copyright © by the author(s). Published here under license by The Resilience Alliance. This article is under a Creative Commons Attribution 4.0 International License. You may share and adapt the work provided the original author and source are credited, you indicate whether any changes were made, and you include a link to the license. ES-2025-16487.pdf
    Research

    ABSTRACT

    Given increasing recognition that strategies to transition to sustainable land use should be context specific, structuring the diversity of land-use agents is important. This is particularly so for the world’s tropical deforestation frontiers, where rapid land-use change, driven by diverse agents, leads to stark social-ecological trade-offs. Focusing on the Argentinean Dry Chaco, a global deforestation hotspot, we employed archetyping to identify key types of land-use agents using data from a questionnaire survey covering three main dimensions: agents’ capital assets (what they have), agents’ activities and management (what they do), and agents’ personal characteristics (who they are). We identified five well-differentiated types of land-use agents: forest-dependent smallholders, semi-subsistence ranchers, crop–livestock farmers, agribusiness farmers, and commercial ranchers. Characterizing these major agent types yielded three main conceptual and methodological insights. First, we reveal considerable heterogeneity of land-use agents in the Argentine Dry Chaco, allowing us to move beyond the common yet oversimplified and dichotomic view of agribusinesses vs. smallholders. Second, the agent typology based on all three dimensions captured the diversity of agents much better than any one-dimensional typology alone, demonstrating the value of richer descriptions of land-use agents. Third, all our agent types share characteristics in some dimensions yet differ in others (e.g., forest-dependent smallholders and crop–livestock farmers were similar in who they are, yet different in what they do), explaining how more simplistic agent descriptions arrive at oversimplified agent types. Overall, our work highlights how archetyping can structure complex human–environment phenomena, diverse land-use agents in our case, for guiding tailored, actor-specific policy interventions.

    INTRODUCTION

    Land use is a main driver of global environmental change and is tightly connected to many of the most urgent sustainability challenges of our times, including climate change, biodiversity loss, and food security (Jaureguiberry et al. 2022). Understanding how and where land use changes, and how these changes impact on social-ecological systems, is therefore important. A promising avenue for achieving a deeper understanding of land-use change is to focus more closely on the agents driving these changes (Malek et al. 2019). This is particularly urgent for the world’s tropical and subtropical regions, where different forms of industrialized agriculture are expanding (Buchadas et al. 2022, Meyfroidt et al. 2024), often into semi-natural landscapes used and inhabited by a range of traditional and local communities (Cáceres 2015, Levers et al. 2021). Although the expansion of industrialized agriculture provides important commodities and contributes to nation’s economies, the social-ecological trade-offs of these land-use changes are typically negative for both the environment and local people (Mastrangelo and Laterra 2015, Barral et al. 2020, Meyfroidt et al. 2022). As a result, many tropical and subtropical regions are in dire need of sustainability planning (Lambin et al. 2014, Schröder et al. 2021).

    Steering social-ecological systems toward sustainability requires a deeper consideration of the people engaged in land use, in other words, the land-use agents (Malek and Verburg 2020). Land-use agents are autonomous individuals with a particular environmental cognition (i.e., values, intentions, attitudes, decision rules) who interact with each other and the ecosystems in the same place and time (Meyfroidt 2013). Understanding and characterizing land-use agents is not trivial, as observed land-use patterns and changes are the aggregated outcome of many individual decisions, made by very different agents, often with diverse cultural backgrounds, capital assets, and motivations (Valbuena et al. 2008, Smajgl et al. 2011). Capturing and representing this complexity is a general challenge in sustainability science (Kuemmerle 2024), yet it is needed to understand land-use decision making and guide the design of conservation and land-use policies (Huber et al. 2024).

    A key challenge is how to structure and organize the large diversity of agent characteristics while avoiding overgeneralization and oversimplification (Meyfroidt et al. 2018). The development of archetypes builds on a long-standing tradition of typological approaches, which have been widely applied in social and rural sciences (McKinney 1950, Jollivet 1965, van der Ploeg 1994), and has gained increasing prominence in sustainability science over the past decade (Oberlack et al. 2019). Archetype analysis offers a robust and adaptable approach for identifying recurrent, empirically grounded patterns that are also theoretically informed. Its strength lies in the capacity to integrate diverse methodological perspectives to reveal context-specific mechanisms, while enabling the derivation of generalizable insights aligned with specific research questions (Eisenack et al. 2021). Archetype analyses can be carried out both in a top-down or bottom-up fashion, each with specific advantages (Food and Agriculture Organization (FAO) 2016, Pacheco-Romero et al. 2021). Top-down, deductive approaches such as expert-based categorization of cases (e.g., land-use agents) have the advantage of being more easily linked to theory, being transferable, and making use of diverse types of data (e.g., qualitative and quantitative data), but require a priori knowledge on the number of archetypes (Oberlack et al. 2019, Pratzer et al. 2024). Conversely, bottom-up, inductive approaches such as data-driven clustering can discover how cases structure into archetypes (Tittonell et al. 2020, Vallejos et al. 2020). Importantly, the relative strengths of both approaches can be combined, and comparing top-down and bottom-up archetyping can be highly informative (Pacheco-Romero et al. 2021).

    Archetyping will inevitably lead to reduction and generalization, which is why it is important to start from a broad set of characteristics and classification criteria that describe cases (FAO 2016, Martinelli 2011). Land-use agent typologies have usually focused on the capital assets of landholders (what they have) (Tittonell et al. 2020). However, land-use agents differ from one another not only in their capital assets, but also in how they manage those assets, especially, land (what they do), and in their personal characteristics (who they are) (Valbuena et al. 2008). So far, typologies have either focused on the structural or management characteristics of landholdings, resulting in “farm” typologies, or, conversely, on the personal characteristics of landholders, resulting in “farmer” typologies (Huber et al. 2024). Such simple typifications of land-use agents have a limited capacity to explain the behavior of land-use agents and to capture the emergence of social-ecological phenomena at the regional scale (Lokhorst et al. 2014, Mastrangelo 2018).

    Understanding the diversity of land-use agents involved in land-use changes is particularly urgent for the world’s tropical dry forests and savannas (Pratzer et al. 2024). These ecosystems are often weakly protected and understudied (Schröder et al. 2021), and as a result, many dry forests and savannas have experienced drastic land-use change (Buchadas et al. 2022). Here, we focus on one such region, the Dry Chaco in Argentina, a global deforestation hotspot (Hansen et al. 2013, Vallejos et al. 2015) The combination of rising international demand for agricultural commodities, technological changes (e.g., herbicide-resistant soybean cultivars), and agribusiness-friendly policies stimulated the arrival and expansion of capitalized farmers and ranchers in the Argentine Chaco (Paolasso et al. 2012, Krapovickas and Longhi 2022), creating one of the most drastic social-ecological transformations in the Global South in the 21st century (Goldfarb and van der Haar 2016). Yet, the land-use agent configuration of the Argentine Dry Chaco is highly diverse, as these new actors expand over lands traditionally used by local family farmers and Indigenous communities, who have been carrying out subsistence farming for decades (Morello et al. 2005, Krapovickas and Longhi 2022). Previous studies focused on land-use agents in the Chaco have employed landholder surveys to uncover the heterogeneity of landholders (Mastrangelo et al. 2019), and to capture the different identities, attitudes, and norms of these agents regarding forests and the surrounding landscape (Mastrangelo et al. 2014). Similarly, a few studies have used archetype analyses to identify major types of land-use patterns or social-ecological systems in the Dry Chaco in a top-down fashion, based on aggregate statistics, remote sensing data, or expert consultations (Baldi et al. 2015, Vallejos et al. 2020, Pratzer et al. 2024). What is missing, however, are studies considering a wider range of agent characteristics (Mastrangelo 2018) to produce a bottom-up typology of major land-use agents.

    Two research questions that guided our work were: (i) What are the major types of land-use agents in the Argentine Dry Chaco and what are their characteristics? and (ii) How do agent typologies differ when based solely on capital assets, management, or personal attributes compared with a typology that considers all these dimensions together? To address these questions, we classified and characterized agents in the northern Argentine Dry Chaco over an area of 176,000 km², where we collected information on agent characteristics through in-person questionnaire surveys between 2016 and 2022.

    METHODS

    Study Area

    The Argentinian Dry Chaco comprises an area of about 488,000 km², and extends across several provinces (Vallejos et al. 2021). We focused on the northern part of this region, in the provinces of Santiago del Estero, Chaco, Formosa, and Salta (Fig. 1). The Argentine Dry Chaco was originally covered by savannas and xerophytic, semi-deciduous forest, dominated by hardwood trees such as quebrachos (Schinopsis spp.) and algarrobos (Prosopis spp.) The average temperature varies from 13°C in winter to 26°C in summer. Rainfall occurs during the summer (October to March), whereas July and August are the driest months (Morello et al. 2012).

    There is a large diversity of land-use agents in the study region competing for land access and use, with different cultural backgrounds, who have historically occupied the territory in successive waves. Historically, Indigenous communities have settled and used the Chaco, practicing mainly hunting and gathering activities and subsistence agriculture. Peasant families and small/medium cattle ranchers settled the region in the 19th and early 20th centuries, practicing forest-based grazing and medium-scaled ranching in some areas. Since the 1990s and especially in the 21st century, the expansion of industrial agriculture by capitalized, large-scale farmers and investors from outside the region has been rampant (Morello et al., 2005, Pratzer et al. 2024), rendering the region one of the most active commodity frontiers in South America (Hansen et al. 2013, le Polain de Waroux et al. 2018).

    Survey design and processing of questionnaire

    We developed a questionnaire together with an interdisciplinary group of regional researchers and practitioners. The questionnaire covered internal attributes of landholdings, which are aligned with those outlined by FAO (2016). We distinguished them in three dimensions: (i) capital assets (what they have), (ii) management (what they do), and (iii) personal (who they are) (Table 1). Surveys were conducted by different teams of researchers. In total, we conducted 336 semi-structured in-person interviews between 2016 and 2022 (Fig. 1). We interviewed the head of the landholding or the person who makes decisions about the use of the land. The landholdings were selected through a snowball method, consulting key actors in the area. Our sample was intended to cover the variability in environmental conditions of landholdings (indicated by geographical location) and the range of socio-economic characteristics of landholders (indicated by landholding size). We implemented the questionnaire using the Kobo application (kobotoolbox.org) on tablets. Additionally, to enhance data security, we had a paper version of the questionnaire and a voice recorder as a backup.

    All survey data were digitized, and the attributes were converted into factorial variables for our analysis, homogenizing the responses into categories (Table 1). Some surveys had missing data due to questions not being answered (in total, we had 739 missing values out of a total of 6,318, equaling a missing data rate of 11.6%). To deal with missing data, we first excluded three attributes that had more than 90 missing values. Next, we excluded questionnaire surveys with more than three unanswered questions (out of a remaining total of 15). This led to the exclusion of 15 interviews. Finally, we used the Mice package in R for imputing the remaining missing data (425 values). This package iteratively imputes values for each variable using predictive models informed by the other variables in the data set. It cycles through all variables multiple times until convergence, generating several complete data sets that reflect the uncertainty of the imputed values (van Buuren and Groothuis-Oudshoorn 2011). This resulted in a database of 336 interviews with complete data for 15 attributes (Table 1).

    Archetyping to identify key land-use agents

    To identify agent types and organize them into a typology, we performed a hierarchy cluster analysis with the Ward method (Ward 1963) using all the attributes from the final survey dataset (Table 1). For the clustering, we chose the Gower distance, which can combine variables of different natures (numerical and categorical) in the distance calculation. We then created a dendrogram plot to evaluate and visualize the resulting clustering. Additionally, we performed a multiple correspondence analysis (MCA), a descriptive method to reduce the dimensionality of data, using the FactoExtra package in R (Kassambara and Mundt 2016). The numbers of clusters and subclusters were selected considering the dendrogram itself and testing different options in the MCA. We selected the number of classes by testing the best separation in the dendrogram and in the MCA two dimensions. We evaluated the distribution of frequencies of all the variables to characterize each agent type and derived bar charts to plot each variable according to each cluster and subcluster.

    To compare unidimensional typologies with the full typology, we repeated the clustering process using only attributes from one dimension. This yielded four typologies: one typology based on the full data set covering all attributes, and one based on “what they have, what they do,” and “who they are ” attributes only. We then assessed the similarity of clusters across typologies by calculating the proportion of agents that were in the same cluster. For example, if a cluster of a one-dimensional typology is equal to a cluster in our three-dimensional typology, a ratio of 1 would be calculated. However, if there was no overlap between clusters, the value was 0. We did this for all cluster combinations and visualized the agreement in an overlap matrix.

    RESULTS

    Our clustering analyses identified three main agent types and, nested within, five sub-types (Fig. 2). The MCA confirmed the results of the clustering, identifying five distinct groupings of data, clearly differentiated when represented in a reduced-dimensional space (Fig. 3). The decision for three main types and five subtypes thus provided the best-defined clusters: they were well-separated, balanced in size, and showed minimal overlap in the MCA representation. Given the clear separation of our clusters based on agents’ attributes, we refer to the main clusters as archetypes, and the five clusters identified in our second-order clustering as sub-archetypes.

    Assessing the characteristics of these archetypes and sub-archetypes based on the attributes contained in our survey and interpreting them through the lens of the three dimensions, allowed us to identify and name these archetypes (Fig. 4). The first archetype consisted of semi-subsistence smallholders, comprising 154 cases. Most semi-subsistence smallholders (71%) face insecure land tenure. Most of these farmers do not use machinery (94%) and rely heavily on family labor (85%). More than half supplement their farm income with off-farm work or receive an additional income. Cattle raising is the predominant activity, supported mostly by natural forage. Many semi-subsistence smallholders also raise small livestock, and half of them collect honey. Around three-quarters of agents in this cluster were local and older than 40 yrs, and almost half had been in the land for >15 years (Append. 1).

    This archetype was subsequently split into two sub-archetypes representing different types of semi-subsistence smallholders: forest-dependent smallholders (1a, 98 cases) and semi-subsistence ranchers (1b, 56 cases). Based on what they have, the main difference between these sub-archetypes is that semi-subsistence ranchers have larger landholdings than forest-dependent smallholders. Also, a larger proportion of semi-subsistence ranchers receive an extra income and have extra-family labor, compared with forest-dependent landholders (Fig. 5b,f). Regarding what they do, forest-dependent smallholders mostly use natural forage to raise livestock, whereas semi-subsistence ranchers use mixed sources of livestock forage (Fig. 5i). Also, forest-dependent smallholders produce or collect honey, whereas semi-subsistence ranchers rarely do so (Fig. 5k). There were no strong differences regarding the who they are dimension (Fig. 5l-o).

    Our second agent archetype was the crop–livestock farmer (81 cases). Like semi-subsistence smallholders, the landholdings of most crop–livestock farmers were smaller than 1,000 ha (Fig. 5b). Compared with semi-subsistence smallholders, a larger proportion of crop–livestock farmers had secured their land tenure (i.e., recognition of property rights by the State) and used machinery (Fig. 5c, d). Family remains the primary source of labor, although 37% of crop–livestock farmers employ a mix of family and external workers (Fig. 5e). Crop–livestock farmers rely on farm income and develop diversified farming systems, combining cropping and cattle raising, the latter mostly based on natural forage. They also raise small livestock, and a majority either produce or collect honey (Fig. 5i-k). Regarding the who they are dimension, crop–livestock farmers are local landowners, with 75% having been on their land for >30 yrs. Most were older than 40 yrs (Fig. 5m).

    Our third archetype was the commercial landholder (101 cases). This group was characterized by larger, commercially oriented landholders, with half of them having >2,500 ha of land. These agents have the highest proportion of titled land and use of machinery. Unlike semi-subsistence smallholders and crop–livestock farmers, the main source of labor is external to the family. Fifty-four percent of the agents in this archetype have an additional source of income. Some of them specialize in crops, typically using high levels of input, and others specialize in cattle production (almost 40% without using natural forage). Small animals are kept by 76% of these agents, but commercial landholders do not engage in honey production. Thirty percent of commercial landholders are extra-local (i.e., from another province or another country), almost half of them (45%) were younger than 40 yrs, and 64% have been in the landholding for <15 yrs. Most commercial landholdings are run by administrators (Append. 1).

    The commercial landholder archetype was split into two sub-archetypes: agribusiness farmers (3a, 55 cases) and commercial ranchers (3b, 46 cases). The main difference between these two in terms of the “what they have” dimension was that agribusiness farmers had larger landholdings than commercial ranchers as well as a higher proportion of external labor (Fig. 5b, e). Stronger differences between these two sub-types occurred in the “what they do” dimension: agribusiness farmers specialize in high-input cropping, whereas commercial ranchers on cattle raising (Fig. 5g). Concerning the “who they are” dimension, agribusiness farmers were younger (mostly 20–40 yrs), had spent less time on the landholding (<15 yrs) compared with commercial ranchers, and more often came from another country (27%) or province (25%). Finally, landholdings of most agribusiness farmers were run by administrators, whereas half of the commercial ranchers managed their ranches themselves (Fig. 5l-o).

    The agent archetypes that emerged were dependent on the type and number of dimensions used for classifying agents. The degree of overlap between each unidimensional typology and the three-dimensional typology varied (Fig. 6). The unidimensional typology with a larger overlap with our full, three-dimensional typology was the one based on “what they do” attributes (Fig. 6b), especially for the 1a, 1b, and 2 sub-archetypes (73%, 94%, and 88% overlap, respectively, Fig. 6b). The agribusiness farmer and the commercial rancher types of the three-dimensional typology (3a and 3b) were collapsed into a single type in the “what they have” typology, which overlaps 93% with the former and 76% with the latter (Fig. 6a). The agribusiness farmer type also showed strong overlap with one type of the “who they are” typology (Fig. 6c), highlighting the unique personal characteristics of this agent type.

    DISCUSSION

    Structuring the complexity of human–nature interactions is important to adequately consider it in sustainability research, practice, and policy making. Here, we demonstrate how bottom-up archetype analyses can help to characterize key land-use agents in a global deforestation hotspot in dire need of sustainability planning, the Argentine Chaco, contributing to a growing field of research aiming to characterize key types of actors involved in land-use change, while also filling an important regional gap. Relying on a rich data set of questionnaire surveys, we use hierarchical clustering to build an agent typology based on agents’ capital assets, management activities, and personal characteristics. We found five well-differentiated types of land-use agents: forest-dependent landholder, semi-subsistence rancher, crop–livestock farmer, agribusiness farmer, and commercial rancher (Table 2). Interpreting these archetypes yielded three main insights. First, we reveal considerable heterogeneity of land-use agents in the Argentine Dry Chaco, allowing us to move beyond the common yet oversimplified and dichotomic view of agribusinesses vs. smallholders. Second, the agent typology based on all three dimensions captured the diversity of agents much better than any one-dimensional typology alone, demonstrating the value of richer descriptions of land-use agents. Third, all our agent types share characteristics in some dimensions yet differ in others (e.g., forest-dependent smallholders and crop–livestock farmers were similar in “who they are,” yet different in “what they do”), explaining how more simplistic agent descriptions arrive at oversimplified agent types. These insights are valuable for shaping more nuanced and effective sustainability policies in diverse social-ecological contexts.

    Our classification and characterization revealed considerable heterogeneity in land-use agents in the Argentine Chaco. This allowed us to move beyond dichotomous views of land-use agents commonly found in literature and expert analyses of deforestation frontiers, in the Chaco and in other regions. Generally, there has been a tendency to represent the social landscape in binary ways, focusing on the most contrasting agent types: smallholders vs. agribusiness (Baldi et al. 2015, le Polain de Waroux et al. 2018, Kong et al. 2019). This is probably because their impacts on land cover are easily differentiable by remote sensing (Baldi et al. 2015) and because agribusinesses often replace smallholders (le Polain de Waroux et al. 2016). Although our agent typology is not directly transferable to other regions and would require adaptation to different social-ecological contexts, its ability to represent such context specificity is a strength and reveals nuances that a binary agent classification would otherwise overlook. This is the case for crop–livestock farmers, which, in our analysis, emerged as a homogeneous and well-differentiated group (Fig. 3). In the Chaco, these “intermediate” agents who occupy a position between semi-subsistence and commercial farmers, partially sharing attributes and dimensions with both (Table 2), do not appear in regional typologies based on remote-sensing data (Baldi et al. 2015) or expert opinion, even those that capture a wide diversity of actors (Pratzer et al. 2024). Similarly, these intermediate agents are overlooked in other commodity frontier regions as well (Ordway et al. 2017), pointing to a wider need to “put them on the map” and consider them in sustainability assessments.

    Characterizing our agents based on a wide range of attributes along our three dimensions allowed us to demonstrate that agents are multidimensional entities (FAO 2016), as archetypes change when different subsets of attributes are used to classify and characterize them (Fig. 6), highlighting the importance of careful variable selection and data collection decisions grounded in hypotheses (FAO 2016, Alvarez et al. 2018). Classifying agents on a single dimension or a few attributes often collapses different agents into the same class, which can be misleading for the design of policy interventions and reduces its effectiveness. On the other hand, it allowed us to capture similarities or differences among agents. Although the typology of agents is based on cross-sectional data and captures a snapshot of the social landscape, our results provide insights into processes of differentiation and convergence among agent types. Semi-subsistence smallholders (sub-archetypes 1a and 1b) and crop–livestock farmers (archetype 2), for example, share personal characteristics and differ in “what they have” and “what they do.” More than two-thirds of these agents are of local origin and have spent most of their lives on the landholding, suggesting strong ties to the land that sustainability policies could build on. However, semi-subsistence smallholders mainly raise livestock on untitled land, and crop–livestock farmers integrate livestock and crops under more secure forms of land tenure. This pattern of similarities and differences may have been generated by a process of social differentiation, whereby agents with a common origin diverged in their trajectories because some of them succeeded in titling their landholdings and diversifying their management systems. In contrast, agribusiness farmers (type 3a) and commercial ranchers (type 3b) are similar in their level of assets but differ in “who they are” and “what they do.” This pattern could be generated by the convergence of agents from different origins (mostly extra-local for 3a and local for 3b) and deploying different production systems (crop-based for 3a and cattle-based for 3b) in a commercial orientation and the management of large landholdings.

    Through a simple and replicable methodology, our work provides valuable inputs for design, implementation, and evaluation of interventions aimed at fostering sustainable land use. A strength of this approach lies in its methodological transferability—the archetyping process we carried out here can be readily and easily applied in other social-ecological contexts to generate similar, context-specific insights and avoid oversimplified, top-down typifications. This is particularly relevant given the growing calls for context specificity in policy development and targeting (Kuemmerle 2024). Understanding the diversity of land-use agents and their characteristics allows to design tailored interventions (Huber et al. 2024) as well as to select those with greater potential for effective implementation (e.g., land-use agents with stronger ties to the land, see above). For example, given their orientation toward the commercialization of grain and beef in the international market, the land-use decisions of commercial landholders (archetype 3) could be strongly influenced by supply-chain interventions, such as zero-deforestation laws imposed by importing countries (Lambin et al. 2018), as in the case of the EU Deforestation Regulation (EUDR). Semi-subsistence smallholders, on the other hand, could be targeted by first providing more security tenure, increasing the chances to work with them for long-term sustainability. More secure land tenure can support higher access to credit and financial and technical assistance, all of which can help semi-subsistence smallholders improve their productivity without compromising biodiversity in their landholdings (Mastrangelo et al. 2019, Faingerch et al. 2021). Crop–livestock farmers, in turn, could be strengthened by developing shorter commercialization chains for selling more environmentally friendly products.

    Our methodological approach shows potential but also has some limitations. As in any simplification of reality, some agent attributes were missing. This is the case of the ethnicity of the agents, which, not being considered, did not allow us to identify types of agents captured in other typologies, such as Mennonites (Baldi et al. 2015) and Indigenous communities (Pratzer et al. 2024). Other aspects not incorporated are those at levels of organization above the individual, for example, attributes related to social capital and institutions (Pratzer et al. 2024). Geographic dynamics were not considered, even though agricultural expansion across large regions such as the Argentine Dry Chaco (Fig. 1) follows diverse patterns that likely influence agents’ characteristics and their spatial distribution. Adding attributes capturing social and geographic dynamics would have yielded even more context-specific archetypes and sub-archetypes. However, our approach strives to achieve a balance between gaining a nuanced picture of the social landscape of a frontier region and providing a cost-effective and replicable methodology that allows to do this with the limited data and resources often found in similar frontier regions. Despite this, our bottom-up approach can help to improve understanding of the structure and dynamics of social-ecological systems in general, and deforestation frontiers in particular in at least two ways. On the one hand, the definition of agents in terms of the management of a given portion of the territory enables the mapping of agents, the analysis of their spatial distribution, and, thus, the identification of potential for conflicts and environmental risks. On the other hand, collecting data from agents enables longitudinal studies and a deeper analysis of social differentiation and convergence processes over time.

    Given widespread evidence for unsustainable land use across the globe, developing and implementing policies to transition to more sustainable land-use futures is critically important. To be successful, such policies must address those that manage land—the land-use agents. Here, we show the importance of recognizing agents as multidimensional entities and highlight the need for and potential of accounting for the diverse factors shaping these land-use agents. Considering the diversity of land-use agents is especially relevant in the global commodity frontier regions, such as in many dry forests and savannas, where land use is changing rapidly, where the interactions among agents are influenced by a range of factors from global to local scales, and where these complex interactions create often stark social-ecological trade-offs (Ordway et al. 2017, le Polain de Waroux et al. 2018, Levers et al. 2021). Our approach demonstrates how key agent types—such as crop–livestock farmers in our case—can be successfully identified, even in relatively data-sparse, dynamic situations such as in the Dry Chaco of Argentina. More generally, our study corroborates how archetype analyses can provide pathways for structuring complexity and diversity in human–environment interactions.

    RESPONSES TO THIS ARTICLE

    Responses to this article are invited. If accepted for publication, your response will be hyperlinked to the article. To submit a response, follow this link. To read responses already accepted, follow this link.

    AUTHOR CONTRIBUTIONS

    Melina Faingerch: conceptualization, methodology, formal analysis, investigation, writing – original draft, writing – review and editing, visualization. Tobias Kuemmerle: writing – original draft, writing – review and editing, funding acquisition. Matthias Baumann: formal analysis, writing – review and editing, visualization. Marcos Texeira: formal analysis. Matias Mastrangelo: conceptualization, methodology, formal analysis, investigation, writing – original draft, writing – review and editing, visualization, funding acquisition.

    ACKNOWLEDGMENTS

    We thank all the landholders who answered the questionnaire and all the researchers and technicians participating in the fieldwork. This work is part of the doctoral thesis of the first author at the Programa de Posgrado en Ciencias Agrarias, Facultad de Ciencias Agrarias, Universidad Nacional de Mar del Plata, Argentina. This work received support through the project “Disponibilidad y acceso a especies nativas importantes para la seguridad alimentaria de familias campesinas criollas e indígenas del Impenetrable Chaqueño,” Code: C200 financed by the Ministerio de Ciencia y Tecnología de la Nación from Argentina, by the German Academic Exchange Service (DAAD), as well as by the European Research Council under the European Union’s Horizon 2020 research and innovation programme (grant agreement 101001239 SYSTEMSHIFT, http://hu.berlin/SystemShift). This work contributes to the Global Land Programme (https://glp.earth). We are grateful to the two anonymous reviewers for their valuable feedback and contributions to this manuscript.

    Use of Artificial Intelligence (AI) and AI-assisted Tools

    The manuscript was reviewed using AI-assisted tools to ensure accuracy in grammar and to enhance the clarity of the language.

    DATA AVAILABILITY

    The data and code that support the findings of this study are available on request from the corresponding author, MF. None of the data and code are publicly available because they contain information that could compromise the privacy of research participants. Ethical approval for this research study was granted by Humboldt University of Berlin.

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    Corresponding author:
    Melina Faingerch
    melinafaingerch@gmail.com
    Appendix 1
    Fig. 1
    Fig. 1. Location of the study region in South America (inset), and the locations of the 336 questionnaire surveys of land-use agents conducted between 2016 and 2022. Dark orange shows agriculture-driven deforestation from 1976 to 2023 (from <a href="https://www.monitoreodesmonte.com.ar" target="_blank">https://www.monitoreodesmonte.com.ar</a>).

    Fig. 1. Location of the study region in South America (inset), and the locations of the 336 questionnaire surveys of land-use agents conducted between 2016 and 2022. Dark orange shows agriculture-driven deforestation from 1976 to 2023 (from https://www.monitoreodesmonte.com.ar).

    Fig. 1
    Fig. 2
    Fig. 2. Result of the clustering analyses of 336 questionnaire surveys from the Argentine Chaco. The dendrogram highlights three main clusters (solid line) and, nested within, five subclusters (dotted lines).

    Fig. 2. Result of the clustering analyses of 336 questionnaire surveys from the Argentine Chaco. The dendrogram highlights three main clusters (solid line) and, nested within, five subclusters (dotted lines).

    Fig. 2
    Fig. 3
    Fig. 3. Multi correspondence analysis for the land-use agents characterized by their clusters. The main types are represented by shapes. The subtypes are represented with colors.

    Fig. 3. Multi correspondence analysis for the land-use agents characterized by their clusters. The main types are represented by shapes. The subtypes are represented with colors.

    Fig. 3
    Fig. 4
    Fig. 4. Schematic representation of the archetypes and sub-archetypes located in a three-dimensional space spanned by our dimensions: what they have is represented by their level of capital, what they do is represented by the level of livestock or crop they carry out, and the dimension of who they are is represented by how local or extra-local they are. The location of the archetypes and sub-archetypes is based on the interpreted relative levels of the attributes in each dimension (Table 2).

    Fig. 4. Schematic representation of the archetypes and sub-archetypes located in a three-dimensional space spanned by our dimensions: what they have is represented by their level of capital, what they do is represented by the level of livestock or crop they carry out, and the dimension of who they are is represented by how local or extra-local they are. The location of the archetypes and sub-archetypes is based on the interpreted relative levels of the attributes in each dimension (Table 2).

    Fig. 4
    Fig. 5
    Fig. 5. Relative distribution of values per agent type (as proportion of all cases in a sub-archetype). Agent archetypes and sub-archetypes shown are 1a = forest-dependent landholder, 1b = semi-subsistence rancher, 2 = crop-livestock farmer, 3a = agribusiness farmer, 3b = commercial rancher.

    Fig. 5. Relative distribution of values per agent type (as proportion of all cases in a sub-archetype). Agent archetypes and sub-archetypes shown are 1a = forest-dependent landholder, 1b = semi-subsistence rancher, 2 = crop-livestock farmer, 3a = agribusiness farmer, 3b = commercial rancher.

    Fig. 5
    Fig. 6
    Fig. 6. Comparison of agent typologies when clustering on the full set of attributes (three dimensions) vs. attributes from one dimension only. The intensity of the coloring indicates the degree of overlap, with darker color indicating a stronger overlapping.

    Fig. 6. Comparison of agent typologies when clustering on the full set of attributes (three dimensions) vs. attributes from one dimension only. The intensity of the coloring indicates the degree of overlap, with darker color indicating a stronger overlapping.

    Fig. 6
    Table 1
    Table 1. Description of the dimensions, attributes, and categories of our questionnaire survey.

    Table 1. Description of the dimensions, attributes, and categories of our questionnaire survey.

    Dimension Attribute Description Categories Description of the category
    What they have Production type Orientation of the landholding’s production Commercial The main destination of the production is trade
    Semi-subsistence The main destination of the production is self-consumption or small-scale trade
    Land tenure Property rights over the land Titled All property rights are recognized by the State through the issue of land title
    Possession Without property rights, or with only some property rights recognized by the State
    Adjudication In process of recognition of full property rights
    Rented The form of tenure is the rent of the land for a short term
    Machinery Use or not of machinery (without discriminating the scale) Yes
    No
    Labor type Type of labor on the landholdings External Labor
    Family Labor
    Both
    Landholding size Range expressed in hectares <1000 ha
    1001–2500
    2501–5000
    >5000 ha
    Source of income Sources of income for the livelihood No-extra incomes The main income are from activities related to the farm
    Extra income Agents with extra income from an activity or source other than the farm (e.g., other economic activity, or a subsidy).
    What they do Main activity Main activity identified by the landholders Cattle Raising cattle and small livestock
    Crop All types of crops included
    Mixed More than one main activity
    Management of the crops For the cropping activity: use of different inputs (pesticides, fertilizers, and/or irrigation) Without inputs Cropping without inputs
    High input Agents who use two or more inputs
    Low input Agents who use just one input
    No cropping They do not use inputs because they do not have crops
    Management of the cattle For the cattle activity: source of forage for feeding No cattle Without cattle
    Natural feed Cattle feed on forest forage
    Cultivated Cultivated forage in situ and/or ex situ.
    Mixed source with natural feed Natural forage plus forage ex situ and/or in situ
    Mixed source without natural feed Feed ex and/or in situ, without natural feed.
    Small livestock Breeding of small livestock (e.g., goats, pigs, chickens) for production and/or consumption Yes
    No
    Collection of honey Collection of wild honey for production and/or consumption Yes
    No
    Who they are Time on the landholding Number of years living or working in the landholding <5 yrs
    6–15 yrs
    16–30 yrs
    31–50 yrs
    > 50 yrs
    Age of the landholder Age of the landholder surveyed 20–40 yrs
    41–60 yrs
    > 60 yrs
    Origin of the landholder Where the agent is from This department
    This province
    Another province
    Another country
    Role of the landholder Self-perceived role of the landholder. It has no direct link to the form of tenure. Owner
    Administrator
    Renter
    Table 2
    Table 2. Summary of the key characteristics of the five sub-archetypes.

    Table 2. Summary of the key characteristics of the five sub-archetypes.

    What they have What they do Who they are
    1a - Forest-dependent smallholder They have small semi-subsistence landholdings with insecure land tenure. They mostly have family labor and extra-farm income. They do cattle ranching and raise small animals in the forest as livestock forage. They also collect honey from the forest. They are local landowners, more than 40 yrs old, who have been in the landholding since birth.
    1b- Semi-subsistence rancher They have small semi-subsistence landholdings, but larger than forest-dependent smallholders. They have insecure land tenure. The labor is mixed, and they have an extra-farm income. They do cattle ranching with mixed sources based on forest. They raise small animals and they do not collect honey. They are local landowners, mostly more than 40 yrs old, who have been in the landholding more than 40 yrs.
    2- Crop–livestock farmer They have semi-subsistence landholdings with the adjudication of the land (a previous step for the titled). They don’t have extra income. Half of them have machinery and mixed labor. They do crop–livestock production. When they raise crops, it is without inputs. When they do cattle, they use the forest as the main source of forage. They raise small animals and they collect honey. They are local landowners, with most of them having spent a long time in the landholding. One-third of them have been there since birth. They are mostly greater than 40 yrs old.
    3a- Agribusiness farmer They have large commercial landholdings. They have secure land tenure, machinery, and external labor, and half of them have an extra-farm income. They do mainly high-input agriculture and mixed activities. When they do cattle, they use mixed sources for forage, without natural feed. Half of them raise small animals. They are young administrators (<40 yrs old), with less than 15 yrs in the landholding.
    Half of them are extra-local from other provinces or another country.
    3b- Commercial rancher They have commercial landholdings with large plots.
    They have machinery, mostly have family labor, and they have an extra income
    They do cattle and mixed activities. The cattle are fed with cultivated and mixed forage, but not natural feed. They raise small animals. When they raise crops, they use diverse strategies (high, low, and without input). Half of them are local landowners, and the other half are administrators, who arrived between 16–30 yrs ago to the landholding. They are in general greater than 40 yrs old.
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    Home > VOLUME 30 > ISSUE 3 > Article 28 Research

    Urban African food systems as sites of challenges and opportunities for household food equity and resilience

    Hannah, C., J. Blekking, J. Davies, J. Battersby, A. Chilenga, D. Kabuya, and P. Toriro. 2025. Urban African food systems as sites of challenges and opportunities for household food equity and resilience. Ecology and Society 30(3):28. https://doi.org/10.5751/ES-16259-300328
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    • Corrie HannahORCIDcontact author, Corrie Hannah
      Arizona Institute for Resilience, University of Arizona
    • Jordan BlekkingORCID, Jordan Blekking
      Department of Earth, Environmental, and Geographical Sciences, University of North Carolina at Charlotte
    • Julia Davies, Julia Davies
      Arizona Institute for Resilience, University of Arizona
    • Jane BattersbyORCID, Jane Battersby
      Environmental and Geographical Science Department, University of Cape Town
    • Allan Chilenga, Allan Chilenga
      Zambia Agriculture Research Institute, Ministry of Agriculture
    • Dorcas Kabuya, Dorcas Kabuya
      National Agricultural Information Services, Ministry of Agriculture
    • Percy ToriroPercy Toriro
      University of Zimbabwe

    The following is the established format for referencing this article:

    Hannah, C., J. Blekking, J. Davies, J. Battersby, A. Chilenga, D. Kabuya, and P. Toriro. 2025. Urban African food systems as sites of challenges and opportunities for household food equity and resilience. Ecology and Society 30(3):28.

    https://doi.org/10.5751/ES-16259-300328

  • Abstract
  • Introduction
  • Methods
  • Results
  • Discussion
  • Conclusion
  • Acknowledgments
  • Data Availability
  • Literature Cited
  • equity; food policy; food security; resilience; urban food systems; urban planning
    Urban African food systems as sites of challenges and opportunities for household food equity and resilience
    Copyright © by the author(s). Published here under license by The Resilience Alliance. This article is under a Creative Commons Attribution 4.0 International License. You may share and adapt the work provided the original author and source are credited, you indicate whether any changes were made, and you include a link to the license. ES-2025-16259.pdf
    Research, part of a special feature on Enhancing Social-Ecological Resilience and Equity in Southern Africa: insights from Research and Practice

    ABSTRACT

    Food and nutrition security remain a significant challenge in Southern Africa’s urban food systems (UFS), where most urban households buy rather than grow their food. UFS comprise a hybrid mix of household food sourcing opportunities from retailers, including open-air markets, street vendors, shops, and supermarkets, as well as household-level strategies, such as urban agriculture. UFS thus bridge the divide between sites of food production and consumption. Yet, the efficacy and equity of UFS in Southern Africa are threatened by climate change, conflict, and disease, among other challenges. At the same time, ongoing nutrition transitions are rapidly transforming UFS environments in ways that are difficult for policymakers to anticipate. With a framing of equity and resilience, we present an empirical case study of how the COVID-19 pandemic affected UFS based on household survey data from 14 small, remote, connected, and larger secondary cities in Zambia. We conducted descriptive and regression analyses to assess what types of households in different city types adopted urban agriculture and bought food at open-air markets, vendors, local shops, and supermarkets in 2019, 2020, and 2021. Households from diverse socioeconomic quartiles perceived similar challenges to maintaining food security and coped with food insecurity in different ways, depending on their capacities and the resources available to them. Diverse households also navigated food sourcing options in UFS in unique ways during the early pandemic years across diverse secondary cities. Households in smaller and remote cities tended to source food from open-air markets, vendors, and urban agriculture, whereas households in more connected cities purchased food from local shops. In consideration of the diverse household and city-scale needs, we contend that creating more resilient and equitable UFS in Zambia and Southern Africa necessitates a comprehensive and adaptable approach to urban policy and planning that recognizes the interconnected and mutually reinforcing relationship between UFS and household resilience.

    INTRODUCTION

    Food and nutrition security are salient concerns in Southern Africa (FAO et al. 2018, FAO, UNECA and AU Commission 2021), which also experiences some of the highest rates of urbanization in the world (Zimmer et al. 2020). Most urban households in the region purchase their food rather than grow it (Davies et al. 2021), which means that urban food systems (UFS) bridge important divides between sites of production and consumption (High Level Panel on Experts on Food Security and Nutrition [HLPE] 2020, Haysom and Battersby 2023). In this paper, we use the 2020 HLPE on Food and Nutrition Security’s definition of UFS, where UFS comprise a hybrid mix of household food sourcing opportunities from retailers, including open-air markets, street vendors, local shops, and supermarkets, as well as household-level strategies, such as urban agriculture and food sharing.

    UFS in Southern Africa contend with multiple challenges that affect the provision of sufficient, affordable, nutritious, safe, and culturally appropriate food to urban consumers, including challenges related to climate change, conflict, socioeconomic inequities, and public health (Ziervogel and Frayne 2011, Clapp and Moseley 2020, Josephson et al. 2021, Abu Hatab 2022). For instance, the COVID-19 pandemic highlighted and exacerbated already existing and longstanding inequities across public and private sectors, societies, and geographies (Laborde et al. 2020, Moseley and Battersby 2020, Joshi et al. 2022). Lockdowns across the globe, including in Africa, presented new challenges to food availability and access, particularly for lower income consumers who lacked the capacity to adapt to shocks and stressors (Dombroski et al. 2020, Bisoffi et al. 2021, Carey et al. 2021). The Russia-Ukraine conflict further contributed to increased food, fertilizer, and energy prices, which placed pressures on global food supply chains with adverse outcomes in sub-Saharan African countries (Abu Hatab 2022, Alexander et al. 2023). At the same time, climate change continued to exacerbate inequalities via a combination of slow-onset pressures (e.g., drought) and sudden-onset disasters (e.g., flash flooding) (Rusca et al. 2023). These pressures and disasters can have adverse impacts on urban food retailers, depending on where the event(s) occur and the type of agri-food supply chain that these retailers rely on (Blekking et al. 2022). Compounding each of these challenges are ongoing high rates of poverty and food insecurity that co-occur in an expanding urban Southern Africa (FAO et al. 2018, UNECA and AU Commission 2021), where urban populations across the region are expected to grow from about 79 million in 2015 to 204 million people by 2050 (UN-DESA 2018).

    A nutrition transition affecting food security also underlies these exogenous shocks and pressures to UFS in Southern Africa, with implications for equity. Across the world and in Africa, scholars have observed an increase in dietary diversity and a rise in “Western style” diets (e.g., rich in fat and refined carbohydrates) (Reardon et al. 2003, Dixon et al. 2007). In Southern Africa, nutrition trends depend on the specific urban location and the diversity of food retailers present. Some urban households still purchase most of their food from open-air markets (Tuholske et al. 2020, Hannah et al. 2022), whereas those in other cities purchase at a greater rate from supermarkets, which tend to offer more processed foods, animal products, and other “Western style” foods (Khonje et al. 2020, Otterbach et al. 2021). Although open-air markets traditionally sell whole foods (e.g., fresh produce), these retailers are increasingly adapting to consumer needs by selling processed foods, sometimes produced by the growing food processing sectors in the countries where these markets are located (Reardon et al. 2021). The nutrition transition of Southern African UFS has specifically occurred alongside a transformation of the food retail environment in cities, which is largely driven by the confluence of the economic interests of real estate developers, private finance, and investors (Battersby 2017). This financialization of UFS has expanded the role of investors and larger commercial food retailers, like supermarkets, leading to higher food prices and high price volatility with disproportionate implications for food security among poor and vulnerable populations (Isakson et al. 2023). The result is an UFS development process that is less inclusive of the diverse socioeconomic populations who rely on these systems for food provisioning.

    Given the compounding shocks and stresses to UFS and an underlying urban nutrition transition in Southern African UFS, what opportunities exist to address uneven access to food and improve urban food security outcomes?

    From a theoretical angle, cultivating a resilience perspective is one approach for identifying pathways to cope with shocks and pressures in a variety of social-ecological systems contexts (Biggs et al. 2015, Hamann et al. 2018, Reyers et al. 2022, Rockström et al. 2023). Seven specific core principles are proposed to help build resilience: (1) maintain diversity and redundancy, (2) manage connectivity, (3) manage slow and fast variables, (4) foster complex adaptive systems thinking, (5) encourage learning, (6) broaden participation, and (7) promote polycentric systems (Biggs et al. 2015). These resilience principles have been applied to core challenges that often arise in food systems (i.e., environmental and nutritional decline, food insecurity and trade, inequity and governance, food systems illiteracy) to illustrate pathways to future food systems resilience (Wood et al. 2023). However, the applicability of resilience principles to the day-to-day governance of UFS remains formidable for planners and policymakers who need swift, actionable solutions to context-specific UFS challenges, like those described above, as well as the financial backing to implement these solutions.

    From the resilience development programming angle, which focuses on household food security, applied research efforts have focused on evaluating the absorptive, adaptive, and transformative capacities of households to mitigate the adverse development consequences of future shocks and stresses (Constas et al. 2014). Across resilience theory and development practice, significant efforts have developed ways of theorizing and measuring these enabling resilience capacities among individuals and households (Barrett et al. 2021, Constas et al. 2022, Smith and Frankenberger 2022). Recent efforts in the resilience measurement space have reviewed a suite of principles, frameworks, and caveats to a resilience measurement agenda of food systems (Béné et al. 2023). Even with these variable measurement tools, common themes and findings persist. For instance, households of lower socioeconomic standing and female-headed households tend to be more food insecure relative to higher income and male-headed households (Modirwa 2011, Caesar and Riley 2018, Bulawayo et al. 2019, Akalu and Wang 2023), but further research is needed to identify pathways for addressing these inequities in UFS.

    Despite significant contributions to the theory and measurement of resilience and food security in the context of food systems (Béné and Devereux 2023), explicit considerations of equity and resilience and how to govern UFS in recognition of widespread inequities are nascent in the academic literature. Moreover, it is not yet clear how UFS in the Southern African context can equitably support urban populations to meet their nutrition and food security needs. To address this knowledge gap, we pose the following research questions:

    1. How do socioeconomic inequities occur among urban households in Southern African cities?
    2. How do low- to middle-income urban households in Southern Africa navigate their local UFS in the context of the COVID-19 pandemic, and do household approaches vary across different cities?
    3. What role can policy and planning play in promoting equitable and resilient UFS in a Southern African context?

    We first consider the existing literature on equity and UFS with a focus on Southern Africa’s smaller urban areas. Secondary cities are growing rapidly on the African continent, with cities of fewer than 500,000 people now hosting two-thirds of all urban population growth (UN-DESA 2014, Pieterse et al. 2015). The UFS of these smaller cities are under increasing pressure to ensure their local constituents are food secure, but there is a relative lack of data on UFS in secondary cities compared to larger primary cities or capital cities (Riley and Crush 2023). Then, we provide an empirical case study of how households in Zambia’s smaller urban areas navigated their UFS in the initial stages of the COVID-19 pandemic using household survey data that was collected across 14 secondary cities over the three time periods of 2019, 2020, and 2021. Rather than operationalizing equity and resilience in the data analysis, we focus instead on presenting a portrait of these diverse UFS, including how households across socioeconomic groups perceive challenges to maintaining food security and how they navigate their UFS over time. In the Discussion section, we use the theoretical concepts on equity and resilience with local knowledge of Zambia’s UFS (and UFS in the wider Southern African region) to consider the implications of the empirical case study for promoting household and UFS resilience.

    Finally, in our discussion we examine how UFS policy and planning could address these inequities. Our investigation is a collaborative research effort between partners from multiple Southern African countries, including Zambia, which supports a resilience-action agenda for urban resilience. Co-production of research findings is essential for identifying context-specific solutions and relevant pathways for promoting equity and resilience in UFS (Sitas et al. 2021). Thus, this research paper was co-produced amongst researchers with food systems expertise in the African context and colleagues in the Ministry of Agriculture in Zambia as part of the 2022–2023 Southern African Resilience Academy. Results of the study were shared in outreach campaigns with relevant urban planners and policymakers in the 14 cities where the research was conducted. Co-produced communications materials included a policy toolkit for Zambian urban planners and policymakers and a policy note for the wider Southern African region. The entire process of co-producing research and engaging with relevant planners and policymakers to identify and discuss contextually relevant solutions was especially formative to the information presented in the Discussion and Conclusion sections.

    UFS in Southern Africa

    Food systems encompass a suite of human-environment interactions related to food production, processing, packaging, distribution, retail, and waste management (Ericksen 2008). As countries urbanize, the food supply chains that food systems rely on become longer and increasingly complex as they connect agricultural production areas with UFS (Barrett et al. 2022). UFS are geographically situated in areas of highly concentrated consumer demand and therefore shape the dynamics of the wider food system via consumption demands and higher amounts of purchasing power (Reardon et al. 2012, Barrett et al. 2022). Because of this widespread reach and influence of UFS, changes to their functionality and complexity, from either external shocks or an underlying nutrition transition, can substantially alter urban and peri-urban human and environmental well-being, as well as social and political outcomes. These changes can affect how urban residents navigate and acquire food in their UFS, which are often characterized by intersecting socioeconomic, gender, health, and political inequities (Hawkes 2006, Hawkes et al. 2022).

    Food systems are also sites of historical, dynamic, and cross-scalar interactions among many actors, ranging from producers, market traders, informal vendors, wholesalers, modern retailers, consumers, policymakers, and so forth (Ericksen 2008). For UFS in Southern Africa, colonial legacies, local planning efforts, and globalization and financialization trends shape the interactions among these actors (Haysom 2021). Colonial era conceptualizations of how a modern city should function are often pursued to this day, which can further marginalize some populations (Fox 2014, Kiaka et al. 2021). For example, urban cleanliness and order tend to characterize idealist visions of a contemporary African city. This concept of modernity is viewed positively and supports the formal food retail industry in urban development. Conversely, informality is considered unacceptable due to concerns like overcrowding, hygiene, and illegality (Battersby 2017, Battersby and Watson 2018a, 2018b). This marginalizes informal food system actors, including street vendors, despite many lower income households relying on these vendors for daily food provisioning.

    To understand these UFS inequities in a Southern African context, we can draw theoretically on Fraser’s work on justice (Fraser 2000, 2005, 2009) and Leach et al.’s (2018) adaptations of Fraser’s framework of equity in a social-ecological system. In short, equity in UFS can manifest in three forms. First, distributional equity refers to how resources, costs, and benefits are allocated or shared amongst people and groups. For example, urban agriculture has commonly been promoted as a solution to household food insecurity and poverty in African cities (Lee-Smith 2010, Nkrumah 2018). Yet recent evidence from Southern Africa highlights various barriers that can exclude lower income households from growing or raising their own food, such as a lack of access to land, property rights, and farming inputs (Davies et al. 2021).These barriers are unevenly distributed, as households in more affluent suburbs have greater capacity to engage in urban agriculture because of better access to resources (Davies et al. 2021, Matamanda et al. 2022).

    Second, recognitional equity refers to the acknowledgment of and respect for identity, values, and associated rights. The Food and Agriculture Organization’s HLPE on Food and Nutrition Security recently proposed including agency as a dimension of food security, in addition to availability, accessibility, utilization, and stability (HLPE 2020). Reflective of recognitional equity, agency within the context of food systems refers to the ability of people to make choices about what to eat; how the food they consume is produced, processed, and distributed; and where they purchase that food (Clapp et al. 2022). The UFS environment can especially impact household agency around food access when local food retailers are displaced by commercial chains and food systems dynamics prioritize processed foods (Dixon et al. 2007).

    Third, procedural equity highlights how decisions are made, and the extent to which different people and groups can influence these decisions or ensure that their perspectives are represented or incorporated in decision-making processes. Procedural equities can be compromised, alongside food security and limiting market participation in the UFS, if forms of localized feedback on UFS policy and planning are not incorporated. Procedural equity is especially pertinent in consideration of the increasing concentration of power by food system actors, such as large, industrialized food retailers (e.g., see Battersby 2017). Yet, informal actors, such as street vendors, often play an important role in the UFS of Southern Africa but are not always incorporated into UFS policy and planning decisions (Toriro 2019, Giroux et al. 2021). Politics and municipal governance in some African cities can influence which actors are recognized or not in an UFS. In cities like Accra, Dakar, and Lusaka, the safety and well-being of informal vendors, who are often vulnerable and working in unsafe conditions, have been forcibly excluded from the UFS with extreme cases of crackdowns and violence (Resnick 2019). Overlooking the important contribution of diverse actors to the UFS can have devastating consequences for urban household employment and food security.

    Although it is helpful to have a conceptualization of equity in UFS, the greater challenge is to develop systems of UFS governance that incorporate the three forms of equity described above. Although UFS serve urban consumers from across the socioeconomic spectrum, UFS in Southern Africa are often not developed with the intention of ensuring equitability in all its forms. For instance, urban planners often endorse investment by large chain supermarkets and shopping malls, viewing them as symbols of urban modernization that stimulate local economic growth (Skinner 2016). However, the pricing and quantities of food in formal retail outlets like supermarkets often cater to middle- and upper-income urban residents who can afford to buy in bulk, inadvertently excluding lower income households that rely more on traditional markets and informal vendors for their food purchases (Peyton et al. 2015, Berger and van Helvoirt 2018). UFS in Southern Africa thus face ongoing equity challenges across household, neighborhood, retail, and city scales.

    A further challenge to addressing equity challenges in UFS is that the development and coordination of UFS are not always explicit mandates for urban planners. Urban development plans are also often created independently of UFS consideration, even though urban planning impacts food systems in several ways (Haysom 2021). For instance, a study of 91 policies in South Africa found that policies relevant to food systems governance were often developed in silos and the diverse stakeholders did not often coordinate in the implementation of policies (Kushitor et al. 2022). Unfortunately, if urban policymakers and planners are indifferent toward food-related planning, then food-related outcomes may be negative, not neutral (Pothukuchi and Kaufman 1999). Thus, UFS policy and planning may be central to fostering the resilience of households to equitably recover from and adapt to the impacts of shocks and stresses.

    METHODS

    We use equity and resilience as the theoretical lens to consider challenges and opportunities for maintaining food security in Southern African UFS. Our approach centers on the presentation of an empirical case study based on household survey data of how socioeconomic inequities occur among households in UFS in 14 smaller, secondary cities in Zambia, how these inequities shape perceptions of sustaining household food security, and how these different households navigated their UFS environment under the shock of COVID-19. Although equities can present in a myriad of ways in UFS (Hawkes 2006, Hawkes et al. 2022), we focus on socioeconomic inequities at the household-level as the principal framing of equity for presenting information on the localized perspectives of food security and resilience in our Zambia UFS case study.

    We present an empirical portrait of UFS in Zambia’s secondary cities. Due to limitations with the availability of consistent data in the 2020 and 2021 survey periods and the nascent state of theory on how equity and resilience are relevant to UFS governance, we do not operationalize equity or resilience in our analysis. Instead, we use an inductive, theory-building approach (Eisenhardt 1989, Volmar and Eisenhardt 2020). We observed patterns among households and cities in our case study and coupled these observations with additional insights from the authors’ existing knowledge and the academic literature to sharpen existing theoretical constructs of equity and resilience in UFS. We use the Discussion section to reflect on our research in the context of our case study and offer theoretical observations that can be further explored and tested in future studies on UFS.

    Urban household survey

    Our survey dataset consists of 657 household surveys collected in June–July 2019, February 2021, and August 2021 from 14 secondary cities in Zambia (Fig. 1). We discuss these surveys based on when they were designed, using the years 2019, 2020, and 2021, respectively. The secondary cities in our sample were Batoka, Choma, Chongwe, Itezhi-Tezhi, Kapiri Mposhi, Maamba, Mazabuka, Mbabala, Mkushi, Mpongwe, Namwala, Nyimba, Pemba, and Petauke. We identified these specific cities using the Global Human Settlement Population (GHS-POP) dataset (Schiavina et al. 2019). We focused on secondary cities with populations ranging from 5000 to 200,000 people because half of Africa’s urban population is concentrated in urban areas with fewer than 300,000 inhabitants (UN-DESA 2018). Local enumerators who were fluent in local languages conducted the surveys in person in 2019 and over the phone during the 2020 and 2021 surveys. We obtained permission from municipal-level authorities and community leaders, as well as Institutional Review Board approval from the lead author’s home institution, to conduct the surveys based on ethical human subjects-based research protocols (#1804499759).

    The 2019 survey was designed to support a larger project on the impacts of agricultural decision-making and adaptive management on food security. The subsequent 2020 and 2021 surveys were implemented opportunistically to accommodate data collection constraints during the first two years of the COVID-19 pandemic. In-person surveys lasted approximately 45–60 min and phone surveys lasted approximately 20–30 min. Questions asked in the phone survey only included a subset of the questions from the in-person survey to more easily accommodate the limited time availability and personal convenience that an individual would have over the phone versus in person. In the 2019 survey, respondents were asked an extensive series of questions on the following topics: household characteristics, demographics, migration and labor, social capital, community support and food transfers, food consumption scores, food security indices, farming, urban agriculture, food purchasing behaviors, household expenditures, and perceptions of climate and food security challenges.

    However, the 2020 and 2021 surveys asked only a subset of the questions that were posed in the 2019 survey. Thus, the multi-year surveys do not host the types of data that would be appropriate for a longitudinal analysis specific for this paper’s topic. Data relevant to our research that remained consistent across all three survey periods included engagement in urban agriculture and food purchasing behaviors. Household characteristics and demographic data were only collected for households that moved locations between the survey periods. Additionally, questions about the perceptions of food security challenges were only asked in 2019. For this paper, we use household characteristics, demographic, and perceptions of food security challenges data from the 2019 survey and urban agriculture and food purchasing behavior data from all three 2019, 2020, and 2021 survey periods.

    The household sampling approach was informed by the authors’ prior familiarity with the cities and consultations with each city’s local government officials. These officials shared estimates of the total numbers of households and estimated population size in each residential area or each city, as well as contextual information about the city. On the basis of this information, households were purposely selected from low- and middle-income residential areas in the 14 secondary cities in 2019. Compared to higher income households, lower income households are more dependent on UFS for maintaining food security as a function of poverty and other inequalities that are associated with a range of social, economic, political, and environmental drivers (e.g., extreme weather, conflict, price shocks, governance failures, and health-related challenges) (Ziervogel and Frayne 2011, Clapp and Moseley 2020, FAO et al. 2021). In other words, we would expect lower income households to be more vulnerable to UFS shocks. Thus, with an aim to identify how UFS can best support the resilience and equity of those households most susceptible to food insecurity, we focused on low- to middle-income residential areas as our targeted population of interest and sample population.

    Within each residential area of each city, we used a systematic random-sampling approach. A defined number of households relative to the size of the sampling area were surveyed each day. This defined number was determined on the basis of the size of the residential area, which ensured a representative and spatially distributed sample for each residential area. Additionally, households next to one another were not sampled. After sampling a household, an enumerator would skip a pre-defined number of households (based on the daily defined sampling goals) until sampling the next household. If, for example, a residential area was estimated to have 100 households, and the daily quota was 10 surveys, then the enumerators would skip every 10 households. For larger cities, if a residential area was estimated to have 500 households, and the daily quota was 20 household surveys, the enumerators would skip every 25 households. Enumerators were encouraged to work together with the fieldwork team and urban officials to ensure that household sampling was spatially distributed evenly across the residential areas.

    If a household had no available or eligible respondent, then the enumerator continued to each successive house until they were able to carry out the survey and then the process of skipping a set number of households was repeated. Eligible respondents included only individuals over the age of 18 from each household with knowledge of household and household member characteristics. Respondents who did not have in-depth knowledge of the employment and income of other household members were not interviewed. The number of surveys conducted ranged from five to thirty per residential area in each city, depending on the density of the area. Sample sizes ranged from 30 to 300 total households in each secondary city, with the smallest cities (e.g., Batoka) consisting of just one residential area, whereas larger cities (e.g., Choma) had many. This data collection approach allowed for the spatially stratified sampling of households, where the household number sample was proportional to city size.

    Data preparation

    Our final dataset consisted of 657 households that participated in all three surveys. The 2019 dataset consists of 2040 households that participated in the in-person survey. Of these households, 1572 provided a phone number(s), indicating their willingness to be contacted again in subsequent surveys. This set of 1572 households from 2019 served as the sampling population for the 2020 survey. We used a proportional random sample based on the 2019 sub-sample sizes per city to ensure that the same proportion of surveys were collected in each city, while also maintaining enough observations to conduct statistical analysis. The 2020 household surveys were conducted via phone call because of travel restrictions and social distancing policies introduced at the start of the COVID-19 pandemic. All reasonable attempts were made to interview the same household member that was first interviewed in the 2019 survey. In total, 950 households engaged in the 2020 survey, of which 865 households participated in the third survey in 2021. Fewer numbers of households participated in the 2021 survey because of natural attrition rates. Survey participation attrition rates were the highest between the 2019 and 2020 surveys, but between each period there were no clear patterns resulting from this attrition. This allowed us to maintain a proportional sample across study cities.

    To prepare the data for analysis, households with duplicate identification numbers or without any identification numbers were excluded from the combined dataset. Data cleaning and analyses were conducted by using RStudio version 2023.3.0.386. We used an initial listwise deletion approach to remove household observations with missing household identification numbers so that we could work from a complete dataset, resulting in a set of 740 households. The dataset was then reduced by 11 households to 729 because of the exclusion of the outliers of incomes greater than 25,000 Zambian Kwacha per month (i.e., US $1787 at the time of data collection in 2019) and households with more than 14 household members. We determined these threshold numbers in consultation with our Zambian authors as being unexpectedly extreme outliers and not representative of the typical urban Zambian household. In the regression analysis, we used the log transformation of the income variable to account for its non-linear and highly skewed distribution. Taking the logarithm of income is a common analytical approach to stabilize the variance and improve model interpretation of highly skewed variables.

    Then, we excluded the observations for 39 households that moved between the 2019 and 2020 survey periods and 33 additional households that moved between the 2020 and 2021 survey periods. Following this data cleaning, the results presented in this paper are based on 657 observations in the 14 Zambian cities, unless otherwise stated in the Results section. The description of the variables for this final dataset that we used in this paper are presented in Tables 1 and 2. Appendix 1 presents figures with descriptive statistics of the distributions of some household variables by secondary city.

    Urban food systems context in Zambia’s smaller secondary cities

    Like other cities in sub-Saharan Africa (Hannah et al. 2022, Blekking et al. 2023, Fobi et al. 2024), open-air markets are an important food sourcing option in the UFS of our case study (Fig. 2). Based on data collected in 2019, local shops and vendors are also important food sourcing options in most cities, followed by supermarkets (Hannah et al. 2022; Fig. 2). Supermarkets tended to be more prominent as a food sourcing option in larger cities, as well as some smaller cities that are near larger cities (e.g., Batoka and Mbabala, located close to Choma), where households may prefer shopping at supermarkets (Figs. 2 and 3).

    Given this diversity across UFS, we would expect households to exhibit variations in food acquisition patterns in response to any given shock, because no single UFS in Zambia is representative of all UFS in the country or across Southern Africa. Households situated in the UFS of smaller cities (e.g., Batoka, Mbabala, Namwala, and Pemba), with no or fewer supermarkets and local shops, could face significant constraints in food purchases if open-air markets were required to close. Households in these cities could then rely more on urban agriculture or street vendors as sources of food. Households in larger sized cities (e.g., Choma, Kapiri Mposhi, and Mazabuka) may have access to a greater diversity of food sourcing options within their UFS, hence shifts in food acquisition behaviors would be contingent on which retailers closed.

    During the early period of the COVID-19 pandemic (2020–2021), laws in Zambia that prohibited street vendors and informal markets from operating in undesignated areas were strictly enforced. However, most businesses dealing with essential goods and services, including more formal open-air markets and supermarkets, were allowed to continue operating (Matenga and Hichambwa 2022, Mudenda et al. 2022, Manda 2023). Although laws mandated certain restrictions and behaviors during the pandemic, insights from our Zambian authors noted that enforcement varied across UFS and even within UFS throughout the pandemic, where some locations were stricter (e.g., Choma) and others more ambiguous, such as in the smaller, more remote cities.

    There were also disruptions in food supply chains due to reduced reliance on imports (e.g., from Zimbabwe and South Africa), as well as health screenings for truck drivers and the disinfection of vehicles that slowed transportation of food (Manda 2023). Supply chain issues resulted in higher food prices, which affected urban consumers’ ability to afford food and maintain food security, especially among households that lost employment in the informal sectors (Matenga and Hichambwa 2022). All of these challenges would likely increase the need for people to rely on alternative food sources, such as engaging in urban agriculture or depending on in-country agricultural systems. Despite these challenges, however, and according to the authors’ perspective, there did not seem to be any clearly available and widespread systematic support during the COVID-pandemic from government programs to adequately target improvements in the UFS.

    Analysis

    Using the survey dataset from 2019, we delineated response groupings based on socioeconomic standing defined by income quartiles. Because urban households most often rely on food purchases to meet their food and nutrition security, we used income quartiles as a socioeconomic lens to guide our analysis. These income quartiles were calculated on the basis of households’ adjusted household income. The total income from all household members were aggregated from their respective incoming salaries, rents, remittances, informal business revenues, and social grants. Then, we divided this sum by the square root of the total number of household members. This approach distributes the incomes across the sampled households in a way that income is not disproportionately affected by differing household sizes (OECD 2011). Households were most often headed by males (488 households, 74%) compared to females (169, 26%).

    First, we examined the relationship between socioeconomic standing and food security in our dataset. Across all households, we assessed the association of household socioeconomic standing via income quartiles and food security using the reduced Coping Strategy Index (rCSI) scores, where a higher rCSI score suggests greater food insecurity. With significant existing evidence that shows that food insecurity is most often associated with socioeconomic standing, we disaggregated our data by gender of the household head to illustrate the intersectionality of female-headed households with socioeconomic standing in the context of household food security. We conducted this analysis for only the baseline year of 2019, because that was the only year for which the rCSI was collected.

    We used rCSI as a proxy measure for household food security because rCSI evaluates household reactions to limited food availability and accessibility during a seven-day period. The rCSI is calculated on the basis of the number of days a household has experienced five coping strategies in the prior seven days from when the household was surveyed. The coping strategies include relying on less preferred or less expensive foods, borrowing food or relying on help from friends or relatives, limiting portion size at mealtime, restricting consumption by adults for small children to eat, and reducing the number of meals eaten in a day. A weighted rCSI score ranges from 0 to 56, where scores ranging from 0 to 3 indicate no to low coping, 4 to 9 indicate medium coping, and greater or equal to 10 indicate high coping and high food insecurity.

    Second, we investigated how urban households perceive challenges as they relate to food security from a disaggregated perspective of socioeconomic standing via the 2019 income quartiles. In the 2019 survey, we asked households, “What are your three biggest challenges with regard to maintaining this household’s food security?” Enumerators posed the question so that respondents had an open-ended response. The enumerator then recorded the key topics, which were post coded as follows: food is too expensive / cannot afford; socioeconomic security (e.g., loss of employment, no income, low income, not enough money, lack of job opportunities, poor economy, school fees, high prices, household demographics - large household, not in labor force); health and food concerns (e.g., there is not enough diversity of food available that I both enjoy and can afford and the food that I have access to is not safe / poor quality); climate- or weather-related challenges (e.g., drought, flood, storms, high temperatures); and do not have any challenges related to food security.

    Finally, we considered the ways in which households across the 14 secondary cities in Zambia bought their food from retailers and produced their own food via urban agriculture in the context of the COVID-19 shock to these UFS. Because of the multi-year nature of our data, we can use COVID-19 as an example of an acute shock to the UFS, understanding that similar other shocks or pressures could similarly impact UFS. Urban household food security is largely contingent on access to the food retail sector or households’ ability to grow their own food. When we assessed the overall food purchasing patterns of sampled households across the survey period, we saw a general decrease in the total number of purchases made in a 14-day period from open-air markets, street vendors, and small retail shops. Thus, to assess the variation of how households navigate UFS across different cities, we aggregated household visits to urban retailers and engagement in urban agriculture by city.

    Then, we conducted regression analyses to assess the relationship between what types of households engaged in urban agriculture and frequented open-air markets, vendors, local shops, and supermarkets over the 2019, 2020, and 2021 survey periods. All models serve as a correlation analysis to explore relationships between variables rather than to establish causation. We employed binary logistic regression models for investigating which types of households engage in urban agriculture (1 = engaged in urban agriculture, 0 = not engaged). Then, we used multiple multivariate regression for assessing which types of households frequented open-air markets, vendors, local shops, and supermarkets in the past two weeks. For all models, household characteristics and demographics were obtained from the 2019 survey as the independent variables. Data on these elements were not collected from our sample population of households that did not move over the survey periods. Thus, the significant underlying assumption of our models is that these 2019 household variables remain the same or similar over the three 2019, 2020, and 2021 survey periods.

    We additionally included binary control variables on the secondary cities to further link our household analysis with the UFS and consider which types of cities tend to be related to greater or lesser engagement in urban agriculture and frequenting of various food retailers. By situating our analysis across different-sized secondary cities, we can consider how a shock or pressure, like COVID-19, could affect households’ food acquisition behaviors at the UFS-level. We adopt the city cluster types that were established in Hannah et al. (2022) using a Principal Component Analysis as follows: Mbabala, Batoka, and Pemba are considered smaller cities; Mpongwe, Namwala, Maamba, and Itezhi-Tezhi are remote mid-sized cities; Nyimba, Petauke, Chongwe, and Mkushi are connected mid-sized cities; and Choma, Kapiri Mposhi, and Mazabuka are larger secondary cities. In our models, we used the larger secondary cities grouping as the reference category for comparing results. All models were run with robust standard errors and tested for multicollinearity. Observations containing missing data were excluded from the regression analysis by using a listwise deletion approach. Regression results were presented using the stargazer package (Hlavac 2022).

    RESULTS

    We first present the baseline results from our 2019 household survey by highlighting food insecurity differences between household types and income quartiles, disaggregating our data by the gender of the household head. Then we present the results from the same survey regarding self-reported challenges for maintaining household food security. Finally, we provide results using all three household surveys aggregated at the city level and the multivariate multiple regression analyses that investigate how household-retailer purchasing patterns and engagement with urban agriculture changed between 2019 and 2021.

    Socioeconomic standing and food security

    We found important differences between socioeconomic standing and food security coping strategies. Households with lower incomes had, on average, higher rCSI scores than households with higher incomes, according to our baseline data from 2019. When disaggregated by gender of the head of household (Fig. 3), we find that female-headed households in the first income quartile have a median rCSI score of 18, whereas male-headed households in that same quartile have a median rCSI score of 10. The other three income quartile groups have relatively similar median rCSI scores between female- and male-headed households, with each increasing quartile representing a decrease in median rCSI values, indicating increasing food security as incomes rise.

    Although other studies have noted similar results, it remains important to focus on inequities that female-headed households often face compared to male-headed households for two reasons. First, gender-based inequities often disproportionately hamper the ability of women to improve their livelihoods (Dodson and Chiweza 2016). Second, this finding may also indicate that these households contend with fewer income-earning household members, which in an urban setting creates a unique challenge for households to access food, because most food is purchased in the urban context (Davies et al. 2021).

    Household perceptions of maintaining food security

    Figure 4 shows that households perceived similar challenges for maintaining their households’ food security regardless of their income quartile. Although households in the highest income quartile reported no challenges compared to the other income quartiles, the distribution of perceived challenges across all categories follows a similar order. Across all income quartiles, households reported that food prices are the biggest challenge, followed by issues related to the socioeconomic security of the household as a secondary challenge, and climate- or weather-related challenges as a tertiary challenge. Fewer lower income households reported no challenges in maintaining their households’ food security compared to the other income quartiles, which suggests that lower income households were more likely to engage in coping strategies in the face of challenges (e.g., Fig. 3). At the same time, however, some households in the highest income quartile were not immune to food insecurity.

    Regardless of income levels, the perceived barriers to maintaining food security across different types of households were similar (Fig. 4). However, lower income households perceived greater challenges compared to households with higher incomes. Food price and socioeconomic security concerns were the most cited challenges by all households, regardless of their income quartile. These results make intuitive sense as urban household food security is largely the result of food access (Crush and Frayne 2011), which in the urban context is correlated with purchasing power (Reardon et al. 2012, Barrett et al. 2022). Climate was consistently cited among household respondents as the third most common concern for maintaining food security with little to no variation across income quartiles. This suggests a consensus among households in secondary cities that climate remains a persistent challenge to food security, a finding that warrants further investigation.

    Household navigation of UFS in the context of COVID-19

    From 2019 to 2021, we found changes at the city scale regarding households’ food purchasing behavior for four different retailers (Fig. 5). In 2019, the most visited food retailer was open-air markets, with an average of 6.5 visits per 14 days. Specifically, open-air markets were most frequented in Mbabala, Mamba, and Pemba (approximately 11.8, 9.6, and 9.1 visits per 14 days, respectively). Households visited street vendors most in Batoka, Mbabala, and Pemba (5.2, 4.1, and 3.6 times, respectively), whereas households visited local shops the most in Choma, Pemba, and Mpongwe (4.0, 3.2, and 3.0 times, respectively). Supermarket use averaged less than 1 visit per 14 days in all secondary cities, with the highest use occurring in Mazabuka, Kapiri-Mposhi, and Choma. These larger cities are also the only cities within our sample that had a supermarket at the time of data collection.

    With the onset of the COVID-19 pandemic in early 2020, our results indicate an overall decrease in the average number of visits to all retailer types overall, and only a handful of increases in the number of visits. For instance, Mkushi, Mpongwe, and Petauke each had increased purchases from roadside vendors in 2020, which was not the case for open-air markets and local shops. These trends may correspond with local government efforts to manage the spread of COVID-19, efforts by households to minimize their exposure to the virus by visiting markets and shops less frequently, and an overall diminished household income available to purchase food. These households may have sought out roadside vendors in the absence of these other retailers, or their lack of income to purchase food from these retailers may have contributed to the decline in visits.

    On the other hand, supermarkets also had decreased visitation during this time, but this decrease was not as severe as our data show for open-air markets and local shops, which may be a result of fewer households from low- to middle-income neighborhoods going to supermarkets in general. Wealthier households that do go to supermarkets would likely have the income to continue to purchase food from supermarkets despite the socioeconomic pressures associated with the COVID-19 pandemic.

    Our data also indicate a return to pre-pandemic use of some retailers in 2021, while for others the decline was greater. In general, local shop purchasing patterns appear to have rebounded to 2019 values after the 2020 decrease. For open-air markets some cities saw a return to 2019 values for households purchasing food from open-air markets, whereas others remained lower than 2019 values. For instance, households in Chongwe and Kapiri-Mposhi both visited open-air markets at an average of about 4.3 times per 14 days in 2020, but in 2021 that frequency increased to approximately 5.5 times per 14 days, nearly the same number of visits as reported in 2019. On the other hand, data from Maamba and Mbabala show more visits in 2021 compared to 2020, yet the number of visits in 2021 were far below the 2019 values.

    For roadside vendors, Mpongwe households visited roadside vendors approximately 2.9 times per 14 days in 2020, but in 2021 that frequency dropped to about 1 visit per 14 days: slightly lower than the 2019 frequency of 1.5 times per 14 days, on average. Likewise, Choma, Maamba, and Petauke all had substantial decreases in the frequency with which households visited local shops between 2020 and 2021.

    Results from the multivariate multiple regression analysis further highlight the variations between smaller and mid-sized secondary cities in the context of the relationship between household characteristics and food purchasing frequency at urban food retailers (Tables 3 and 4). These regression models are used to assess correlations between the independent and dependent variables rather than to establish causation. Additionally, low adjusted R-squared values across all models suggest that the proportion of variance in the response variables are not well explained by independent variables. Thus, we present these models in an effort to explore possible relationships between variables that can be more carefully investigated in future empirical research.

    Food purchasing behaviors were diverse across all city types and shifted across the survey periods. Reflecting patterns observed in Figure 5, frequent shopping at open-air markets before the pandemic held a significantly positive relationship with both smaller urban areas and remote mid-sized cities in 2019 (relative to larger secondary cities). This relationship was negative in 2020 and positive in 2021 (Table 3). We also observed a positive relationship between connected mid-sized cities (relative to larger secondary cities) and frequency of food purchases at open-air markets and vendors in 2019. This relationship also flipped to a positive relationship in 2021 (Table 3). These shifting trends over time may be attributed to open-air market and vendor regulations during the early stages of the pandemic.

    In terms of household characteristics, there was a positive relationship between female-headed households and purchasing food from vendors following the initial stages of the COVID-19 restrictions (Table 3), which is the only instance where we observed a significant difference between male- and female-headed households in terms of the number of times they went to different food retailers. We also found a significant negative relationship between the log of income and purchasing from these informal food retailers in 2020 for open-air markets and 2019 for vendors (Table 3), which suggests that the locations where households purchase food is dependent upon household income. Increased distance to bus stops was also negatively associated with purchases from open-air markets (Table 3).

    For shopping at more formal food retail vendors, our regression results presented a statistically significant positive relationship between the log of income and frequency of food purchases at both local shops and supermarkets across all survey periods (except for shopping at supermarkets in 2019). Converse to the patterns observed for shopping at more informal retailers, these results suggest that households with more wealth are more likely to shop at supermarkets, which is consistent with the existing literature (Blekking et al. 2023, Fobi et al. 2024). No other household characteristic showed a significant relationship to shopping except for the 2019 survey period for purchasing food at local shops. In this case, increased household size, decreased distance to bus stop, and renting households all presented a negative relationship to purchasing food at local shops.

    Similar to observations for the informal food retail sector, results showed that diverse relationships between different types of cities and purchasing food at local shops and supermarkets. Smaller urban areas were not significantly associated with making frequent purchases at local shops or supermarkets, with the only exception being during the 2021 survey period. Remote mid-sized urban areas were only found to be positively associated with purchasing more frequently at local shops in the 2020 survey, whereas connected mid-sized cities (i.e., cities located in closer proximity to other cities) were found to be negatively associated with purchasing at local shops in 2019. Yet, there was a persisting negative relationship between both remote and connected urban areas and purchasing food at supermarkets across all time horizons. These results are supported by the existing literature that supermarkets do not feature prominently in smaller to mid-sized secondary cities (Hannah et al. 2022, Fobi et al. 2024), even in the context of a shock like the COVID-19 pandemic, where most low- to middle-income households would likely not be able to afford supermarket food prices.

    For these same 14 secondary cities, the use of urban agriculture varied during the study years, and our results suggest both decreases and increases following the onset of the COVID-19 pandemic (Fig. 6). Batoka, Itezhi-Tezhi, Kapiri-Mposhi, Mazabuka, Mkushi, Mpongwe, Nyimba, and Pemba all feature an increase in the percentage of households practicing urban agriculture from 2019 to the 2020 survey. For example, in 2019, about 20 percent of households in Batoka reported growing their own food at home or in their residential area, but after the start of the pandemic, 100 percent reported growing some amount of their own food at home or in their residential area. Apart from Mbabala, which is in a rural area, households shifted significantly to urban agriculture in the smaller sized urban areas (e.g., Batoka, Mpongwe, Namwala, Nyimba, and Pemba) compared to larger sized urban areas that have a greater number of food retail options.

    Of the households that reported practicing urban agriculture in the 2019 survey (42% of all households), most (81%) cultivated food in household gardens and several others (18%) cultivated food at a garden or other location beyond the household. Most households (67%) reported planting dark green and leafy vegetables, followed by maize (38%) and various other plants, such as Irish potatoes, sweet potatoes, cassava, carrots, tomatoes, mangos, bananas, nuts, seeds, and other fruits and vegetables. Very few households reported raising livestock; those included chicken (only 48 households), goat (5 households), rabbit (1 household), and cow (1 household). In terms of scale, only 4 households reported using pots or sacks for planting food and less than a fifth of households (17%) shared that they only have a few plants. Approximately a quarter of households (26%) planted food in an area of less than 6 m² and a fifth of households (20%) cultivated food in an area of 6 to 12 m². Over a third (35%) planted food in an area greater than 12 m², of which 31 households cultivated plants on an area of land greater than 30 m². Based on the authors’ familiarity with the region and field observations, larger plots of land are typically located in the smaller and remote secondary cities that are less densely populated. These larger areas of land typically allow for greater opportunities to plant diverse crops and support livestock.

    Binary logistic regression results further show diverse household engagement in urban agriculture, both across survey time periods and city types (Table 5). In these regressions, additional household variables most relevant to supporting urban agriculture were included (e.g., private water source on the property). Odds ratios are used to interpret the logistic regressions, where ratios greater than one are associated with a greater likelihood of the dependent event occurring as the independent variables increase (e.g., urban agriculture engagement as income increases). Ratios less than one suggest that the event is less likely to occur.

    Overall, we found that those households with greater socioeconomic entitlements (e.g., not renting, larger houses, private water source on property) were associated with engagement in urban agriculture when there was a significant relationship. In 2019, before the pandemic, households in planned settlements, renting households, and households on the electric grid were significantly less likely to engage in urban agriculture. Although not significant, the likelihood of engaging in urban agriculture flipped for renting households in 2020 but then returned to being significantly less likely to engage in 2021, which is consistent with some of the trends observed in Figure 6.

    As the income wealth of households increased, there was a greater likelihood to engage in urban agriculture in 2020. This finding was the only emergent household characteristic related to engaging in urban agriculture following the pandemic, which may be attributed to the ability of wealthier households to absorb shocks and adapt to alternative food production sources within a short timeline compared to lower income households. Across all survey time periods, larger households (e.g., those with an increased number of rooms) and those with a private water source on their property were more likely to engage in urban agriculture. These findings are consistent with some identified barriers to engagement in urban agriculture among lower income households, which are less likely to own land, have access to production resources, and be able to afford the inputs to grow food (Davies et al. 2022).

    Variations in urban agriculture engagement were also observed across city types. Smaller urban areas (relative to larger secondary cities) were less likely to engage in urban agriculture only in the pre-pandemic period. Connected mid-sized cities (relative to larger secondary cities) were also less likely to engage in urban agriculture across all survey periods, which is likely due to households having greater access to a more diverse set of food retail options than smaller and remote cities. Remote mid-sized cities (relative to larger secondary cities) were significantly less likely to engage in urban agriculture before the pandemic in 2019 but then were significantly more likely to engage in urban agriculture during the 2020 and 2021 survey periods. This result may be attributed to being less connected with the wider food system to source food, especially during the pandemic when food supply chains were compromised. These variations in household engagement in urban agriculture, both across time and city types, show how diverse UFS are in the context of a shock like the COVID-19 pandemic.

    DISCUSSION

    Our results regarding the observed socioeconomic inequities across urban households in Zambia align with observations in other parts of Africa (Modirwa 2011, Caesar and Riley 2018, Bulawayo et al. 2019, Akalu and Wang 2023). Lower income households tend to rely on more coping strategies in response to food insecurity, and lower income female-headed households disproportionately engage in more coping strategies compared to all other households. This highlights the heightened vulnerability of lower income and female-headed households to the impacts of different shocks or pressures compared to higher income and male-headed households. Despite these disparities, we found that households from different socioeconomic backgrounds perceived similar overarching concerns, highlighting shared vulnerabilities in the shock context of the COVID-19 pandemic. Beyond these well-established trends, our findings emphasize the role of diverse UFS in offering different food acquisition options to households in different types of cities. Our discussion emphasizes these more novel insights to explore how policy and planning can promote equitable and resilient UFS in a Southern African context.

    A case for equity in UFS planning and policy: Zambia’s Constituency Development Fund

    Across the households included in our study, food prices were perceived as the predominant concern for maintaining food security, even though more vulnerable households are likely to struggle with the rising cost of food to a greater degree. Moreover, fluctuating food prices are a concern for urban households regardless of the driver or origin of that fluctuation. Coupled with the nutrition transition and the financialization of UFS (Battersby 2017), the COVID-19 pandemic, economic effects of the Russia-Ukraine conflict on global food chains, and regional drought impacts on crop production have all recently impacted food prices in Zambia and Southern Africa more broadly (Isakson et al. 2023). Aside from food prices, urban households commonly identified general socioeconomic security and climate to be significant concerns for household food security.

    Despite common concerns about the types of shocks to food security across urban households, and regardless of the nature or origin of a given shock, a more equitable approach for mitigating the impacts of shocks would require UFS policy and planning to provide greater support to lower income and female-headed households to ensure that they have as much capacity to cope with and adapt to shocks as households with higher socioeconomic status. UFS policy and planning can consider Fraser’s three dimensions of distributional, recognitional, and procedural equity (Fraser 2000, 2005, 2009) and Leach et al.’s (2018) adaptation of this equity framing, whereby resources are allocated to support diverse populations (distributional equity), diverse households and food retailers are afforded the authority and agency to engage in their UFS (recognitional equity), and mechanisms are established to design an UFS environment that facilitates food accessibility, affordability, and availability for diverse households in diverse cities (procedural equity).

    For UFS in Zambia, the Constituency Development Fund (CDF) is an example of a national effort that has specific implications for recognitional, distributional, and procedural equity opportunities in UFS. Established under the Zambia Constitution, the CDF Act (2018) sets up the governance mechanisms, such as CDF committees, to manage, disburse, utilize, and maintain accountability of government-appropriated funds for local development initiatives (i.e., distributional equity). The CDF provides opportunities for service delivery to be more responsive to public needs, strengthens decentralized local institutions, and promotes economic development (Casey et al. 2021) (i.e., recognitional equity). The Ministry of Local Government and Rural Development is mandated to coordinate the implementation of the CDF projects and programs through the CDF Committees, Members of Parliament, local authorities, cooperating partners, and members of the community (i.e., procedural equity).

    Although the CDF Act was passed in 2018, the CDF only increased to K28.3 million per constituency in the 2023 national budget to account for inclusive development. Prior to 2023, funding was not sufficient to support the wide range of community development initiatives. Thus, in the 14 cities in our study for the period of 2019–2021, when we collected data, we did not identify any evidence of CDF support that would have improved the UFS. Future studies on UFS in Zambia could investigate the impacts of CDF-supported projects on household and UFS resilience.

    The CDF in Zambia has thus far been used to address several distributional inequities that women especially face in acquiring food safely and engaging economically in their local UFS as producers and vendors. These efforts simultaneously promote women’s agency and ability to participate productively in the UFS, which is a critical component of food security (Clapp et al. 2022a). In Kitwe, for example, a market was constructed specifically for women by using CDF funds, with the aim of providing women with a safe and secure space to sell their goods and access clean water, sanitation, and other essential services. In Ndola, the CDF was used to provide loans to women who are starting food-related businesses. In Kabwe, the CDF supported a project that is training women in urban agriculture and providing them with access to land, seeds, and other agricultural inputs. In Lusaka, the CDF was used to provide training in business management, marketing, and financial literacy to women who are market vendors. Financial support from this CDF has been used to purchase goods, rent stalls, and pay for other business expenses.

    Different city types host diverse UFS and households require diverse UFS

    Our findings further show that different cities require different UFS planning and policy responses to deal with shocks. At the intercity level, we found that the shock of the COVID-19 pandemic had variable impacts on different UFS depending on city type. These differences were evident based on the changes in the frequency of household visits to food retailers over the pandemic period, as well as the reported changes in engagement in urban agriculture in these households. Several characteristics may inform differences in UFS. For instance, some urban areas that are smaller and more remote (e.g., Mbabala, Mpongwe, and Batoka) are less directly engaged with the global food supply chain than larger cities and would therefore be comparatively insulated from global-scale shocks. On the other hand, larger cities (e.g., Choma, Kapiri Mposhi, and Mazabuka) tend to be more connected to global food supply chains and would thus be more sensitive to global shocks, such as COVID-19 and the conflict in Ukraine.

    These dynamics are further influenced by the varying characteristics and structures of UFS in different-sized cities, which shape their resilience to shocks and stressors. For instance, larger secondary cities often feature more opportunities for households to earn cash income that can be used toward food purchases, as well as more diverse food retail systems that include formal supermarkets, local shops, open-air markets, and street vendors. This diversity enhances resilience by providing households with multiple food sourcing options, enabling them to adapt more easily to disruptions in any single supply chain. In contrast, smaller secondary cities may rely more heavily on informal markets and urban agriculture, which allows for closer networks to local agricultural producers. These networks can contribute to resilience by offering a more localized and potentially stable food supply during external shocks.

    Whereas the proximity of smaller secondary cities to rural agricultural areas may buffer food insecurity risks during large-scale economic shocks, smaller, more remote urban areas would be more sensitive to localized shocks, including climate extremes such as droughts, floods, and heatwaves. Because these smaller cities would likely have a more limited diversity of food sourcing options, households would need to seek out alternative food acquisition strategies, such as engaging more in urban agriculture. Larger cities also have a comparative advantage because of their capacity to host a greater diversity of food acquisition options, which may enable households of average or greater socioeconomic standing to adapt and be resilient to these kinds of shocks. The resilience of UFS in different-sized secondary cities is thus not determined by a single factor, such as retail diversity or connectivity to rural agricultural networks. Rather, UFS resilience emerges from the interplay of various elements, including the diversity of food sources along with infrastructure quality, governance, and the adaptive capacities of households.

    Diverse UFS require diverse UFS planning and policy approaches

    Given the diversity of cities and their UFS in Zambia, and Southern Africa broadly, urban policymakers and planners will need to draw from a variety of options to respond to a given shock in an equitable manner. Complementary to diversity, UFS and household resilience to food-related shocks is not contingent on access to food, in general, but rather sustained access to healthy and nutritious foods over time (Clapp et al. 2022). To some degree, the nutrition transition has been occurring due to a lack of equitable planning (Battersby 2017), where larger agri-food actors do not always take into consideration the importance of nutrition and balanced diets. This nutrition transition also likely varies across cities. With compounding challenges to local UFS globally and the underlying nutrition transformation, maintaining a diverse food system to meet diverse households is critical (Béné and Devereux 2023).

    In Zambia, there are several policies that may be relevant for helping strengthen the resilience of UFS, including some that may not be explicitly designed with UFS in mind. For instance, the Markets and Bus Stations Act is a national policy with important local implications. The Act sets up the governance structures for open-air markets, which play a critical role in the UFS of most urban areas in Zambia (Hannah et al. 2022). Supporting investment in these markets and including market committees in city-level policy and planning processes can help address the recognitional equity aspect of markets that is often missing in UFS planning. The Zambia National Lands Policy supports government agencies, such as the Department of Town and Country Planning, to promote sustainable land management and equitable access to land. This includes making provisions for land tenure, water accessibility, and the availability of agricultural inputs, all of which are necessary for households to engage effectively in urban agriculture (Davies et al. 2020). Further relevant policies in Zambia are presented in Table B1 of Appendix 2.

    As each UFS is unique, our survey data alone do not allow us to draw precise conclusions about the variability in UFS across cities, nor about shifting household behaviors, such as changes in visits to food retailers or levels of urban agriculture engagement. However, the variation in changes that we observed across different cities from 2019 to 2021 suggests a need for flexible, context-specific responses to shocks and pressures, whereby interventions can be adapted to meet the needs of diverse household types and different cities. To achieve this approach, it is important to consider the unique strengths and vulnerabilities of each city, including how decision-makers support cities in response to shocks, which can affect how households respond to food insecurity challenges.

    Policy tools such as the CDF can help address equity challenges by serving as a reinforcement system to support households in times of need, thereby strengthening the resilience of households and UFS to future shocks. Simultaneously, policy tools should aim to incorporate the perspectives and voices of all relevant stakeholders to ensure recognitional and procedural equity in UFS governance. In some cities, street vending and urban agriculture contribute significantly to food accessibility, affordability, and availability. Establishing clear guidelines and providing resources and training to vendors and urban farmers and fostering collaboration between local government authorities and relevant national ministries are essential actions for promoting safe and organized street vending and supporting urban agriculture. These collective efforts can build more resilient and equitable UFS that ensure food security and well-being for all residents.

    Finally, policies aimed at strengthening UFS must consider household-level capacities to ensure equity in resilience-building efforts, recognizing that the resilience of UFS and the resilience of individual households are interconnected and can be mutually reinforcing. Our findings demonstrate that the diversity within UFS served as a buffer for some urban households during the COVID-19 pandemic, thereby enhancing household resilience. To assess these relationships, we examined household coping mechanisms alongside UFS dynamics, which included shifts in food acquisition patterns that reveal an interplay between household- and system-level resilience. Strengthening UFS resilience through strategies like supporting diverse food retailers, promoting inclusivity in urban planning, and investing in robust infrastructure expands the ability of households to cope with shocks. System-level approaches, such as the CDF play a critical role by directly funding community-based initiatives that address localized food insecurity and strengthen UFS infrastructure, which builds household resilience. In turn, resilient households contribute to the broader resilience of UFS by maintaining stable demand across diverse food sources and adopting adaptive practices like urban agriculture, which strengthen local food systems. These dynamics underscore the importance of an integrated approach to resilience-building that simultaneously addresses household needs and the functioning of the system as a whole.

    CONCLUSION

    The need for resilient and equitable UFS is critical as Southern Africa faces compounding shocks and stresses alongside an underlying nutrition transition. We focus on socioeconomic inequities at the household-level, which we use as a lens to understand localized perspectives of food security and resilience in the UFS of 14 secondary cities in Zambia. Our findings highlight three key patterns related to resilience and equity in UFS. First, lower income, female-headed households in Zambia are particularly vulnerable to the impacts of shocks and pressures, including those leading to food insecurity, aligning with similar studies from Southern Africa. Second, households across different socioeconomic backgrounds perceive similar challenges, with fluctuations in food prices, socioeconomic security, and climate-related impacts being major concerns. An extension of our research, which focuses only on a subset population of low- to medium-income households, should expand the sample population to also include higher income households to see how they would perceive these challenges. Third, UFS in diverse urban areas provided varying food acquisition options to households during the challenges of the COVID-19 pandemic, suggesting that some households may have coped better based on their city type.

    Policy and planning are central to building UFS resilience and mitigating inequities across households and UFS patterns across cities. Resilient and equitable UFS exhibit diversity and the ability to withstand and recover from shocks and stresses throughout the entire value chain, from production to consumption, while ensuring fair and sustainable access to safe, nutritious, affordable, and culturally appropriate food for all residents within an urban area. Equitable resilience, achieved through building resilience in an equitable manner, enables all UFS users to absorb shocks, recover, and adapt to new conditions. Incorporating equity in all its forms, including distributional, recognitional, and procedural aspects, contributes significantly to resilience building in UFS.

    Creating more resilient and equitable UFS in Zambia and Southern Africa necessitates a comprehensive and adaptable approach to urban policy and planning that recognizes the interconnected and mutually reinforcing relationship between UFS and household resilience. This approach should consider both similarities and differences at household and city scales, encompass various policy areas (including those that may not be explicitly designed to manage UFS), and engage multiple stakeholders in planning and decision-making processes. Aligning and integrating key policies at national and local levels can further address urban food insecurity and enhance UFS resilience. Ultimately, promoting equitable UFS resilience requires an approach that simultaneously addresses household needs and systems-level functionality, wherein policy and planning are central to addressing urban food security challenges more equitably.

    RESPONSES TO THIS ARTICLE

    Responses to this article are invited. If accepted for publication, your response will be hyperlinked to the article. To submit a response, follow this link. To read responses already accepted, follow this link.

    ACKNOWLEDGMENTS

    This paper was developed as part of the Southern African Resilience Academy, an initiative of the Global Resilience Partnership, with support from the South African Research Chairs Initiative (SARChI) of the Department of Science and Technology and National Research Foundation of South Africa (grant 98766). Data collection was supported by the National Science Foundation (SES-1360463 and BCS-1115009). The Institutional Review Board at the University of Arizona approved the research design (Human Research Protocol #1804499749). The authors express their gratitude to Tom Evans for contributions to funding the research and research dissemination campaign in Zambia, Andrew Zimmer for assistance with the data collection, the Zambia Agriculture Research Institute for their assistance with the field research and leading the dissemination campaign with the National Agricultural Informal Services, and the research participants who contributed their time to this study.

    Use of Artificial Intelligence (AI) and AI-assisted Tools

    No AI generative or AI-assisted technology were used in the process of writing this paper.

    DATA AVAILABILITY

    The data and code that support the findings of this study are available on request from the corresponding author. None of the data and code are publicly available because they contain information that could compromise the privacy of research participants. Ethical approval for this research study was granted by the University of Arizona, Human Research Protocol #1804499749.

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    Corresponding author:
    Corrie Hannah
    corrieh@arizona.edu
    Appendix 1
    Appendix 2
    Fig. 1
    Fig. 1. Locations of where surveys were collected according to their sample size from the 2019 survey.

    Fig. 1. Locations of where surveys were collected according to their sample size from the 2019 survey.

    Fig. 1
    Fig. 2
    Fig. 2. Food retail locations where household respondents spend the most money on food purchases by city size. High density area is calculated based on the number of pixels associated with the Global Human Settlement Population (GHS-POP) dataset for the year of 2015 based within the city’s urban Open-Source Mapping urban footprint (Hannah et al. 2022). Cities with one or more operating supermarkets in 2019 are noted with a starred symbol. Figure adapted from Hannah et al. 2022.

    Fig. 2. Food retail locations where household respondents spend the most money on food purchases by city size. High density area is calculated based on the number of pixels associated with the Global Human Settlement Population (GHS-POP) dataset for the year of 2015 based within the city’s urban Open-Source Mapping urban footprint (Hannah et al. 2022). Cities with one or more operating supermarkets in 2019 are noted with a starred symbol. Figure adapted from Hannah et al. 2022.

    Fig. 2
    Fig. 3
    Fig. 3. Gender disaggregated Reduced Coping Strategy Index (rCSI) scores by adjusted income quartiles, where a higher rCSI score indicates lower food security. Quartile 1 indicates lower income and Quartile 4 indicates higher income. White box plots indicate male-headed households and blue box plots indicate female headed households. The sample size is 657 households from the 2019 survey.

    Fig. 3. Gender disaggregated Reduced Coping Strategy Index (rCSI) scores by adjusted income quartiles, where a higher rCSI score indicates lower food security. Quartile 1 indicates lower income and Quartile 4 indicates higher income. White box plots indicate male-headed households and blue box plots indicate female headed households. The sample size is 657 households from the 2019 survey.

    Fig. 3
    Fig. 4
    Fig. 4. Perceived challenges for maintaining household food security by income quartile. Quartile 1 indicates lower income and Quartile 4 indicates higher income. The sample size is 740 from the 2019 survey and includes households that moved locations during the 2020 and 2021 survey periods.

    Fig. 4. Perceived challenges for maintaining household food security by income quartile. Quartile 1 indicates lower income and Quartile 4 indicates higher income. The sample size is 740 from the 2019 survey and includes households that moved locations during the 2020 and 2021 survey periods.

    Fig. 4
    Fig. 5
    Fig. 5. Frequency of household purchases aggregated by secondary city, ordered from smallest to largest city, from roadside vendors, open-air markets, supermarkets, and local shops during a 14-day period from the 2019, 2020, and 2021 surveys. The sample size is 740 from the 2019 survey and includes households that moved locations during the 2020 and 2021 survey periods.

    Fig. 5. Frequency of household purchases aggregated by secondary city, ordered from smallest to largest city, from roadside vendors, open-air markets, supermarkets, and local shops during a 14-day period from the 2019, 2020, and 2021 surveys. The sample size is 740 from the 2019 survey and includes households that moved locations during the 2020 and 2021 survey periods.

    Fig. 5
    Fig. 6
    Fig. 6. Percentage of household samples that practiced urban agriculture by city, ordered from smallest to largest city, from the 2019, 2020, and 2021 surveys. The sample size is 740 from the 2019 survey and includes households that moved locations during the 2020 and 2021 survey periods.

    Fig. 6. Percentage of household samples that practiced urban agriculture by city, ordered from smallest to largest city, from the 2019, 2020, and 2021 surveys. The sample size is 740 from the 2019 survey and includes households that moved locations during the 2020 and 2021 survey periods.

    Fig. 6
    Table 1
    Table 1. Description of continuous household-level variables and descriptive statistics using the baseline data from the 2019 survey across all cities. Dependent variables for the frequency of food purchases at open-air markets, vendors, local shops, and supermarkets are also included from the 2019, 2020, and 2021 surveys.

    Table 1. Description of continuous household-level variables and descriptive statistics using the baseline data from the 2019 survey across all cities. Dependent variables for the frequency of food purchases at open-air markets, vendors, local shops, and supermarkets are also included from the 2019, 2020, and 2021 surveys.

    Variable type Variable name Description Year Min. Max. Mean Median Std. dev. Missing observations
    Dependent Open-air market food purchases Number of food purchases in the past two weeks from open-air markets measured in days (0–14) 2019 0 14 6.57 5 4.83 1
    2020 0 14 4.33 3 3.19 5
    2021 0 14 4.21 4 2.41 0
    Dependent Vendor food purchases Number of food purchases in the past two weeks from vendors markets measured in days (0–14) 2019 0 14 2.6 1 3.91 37
    2020 0 14 1.91 1 2.42 36
    2021 0 10 1.73 1.7 1.7 40
    Dependent Local shop food purchases Number of food purchases in the past two weeks from local shops measured in days (0–14) 2019 0 14 2.43 1 3.4 24
    2020 0 14 1.66 1 2.13 64
    2021 0 8 1.41 1 1.25 64
    Dependent Supermarket food purchases Number of food purchases in the past two weeks from supermarkets measured in days (0–14) 2019 0 14 0.42 0 1.57 42
    2020 0 14 0.39 0 1.04 98
    2021 0 5 0.37 0 0.7 144
    Independent Reduced Coping Strategy Index (rCSI) Composite score measuring the severity of coping strategies used by individuals or households in the last 7 days to cope with food insecurity. Scores range from 0 to 56 with a higher score indicating more severe food insecurity. Coping thresholds can be interpreted as follows: 0–3 no or low coping; 4–9 medium coping; rCSI ≥10 high coping. 2019 0 56 11.03 7 12.31 17
    Excluded from regression Adjusted household income Total household income adjusted for all incoming salaries, rents, remittances, informal business revenues, and social grants (Zambian Kwacha) 2019 0 11,180.34 1141.96 612.37 1401.5 0
    Independent Log of income Log of adjusted income (Zambian Kwacha) 2019 0 9.32 6.39 6.42 1.32 0
    Independent Household size Number of people living in the household 2019 1 14 5.69 5 2.53 0
    Independent Distance to bus stop Distance from the household to the nearest bus stop measured in minutes walking 2019 0 120 20.29 20 15.28 7
    Independent Number of rooms Number of rooms in the household (excluding kitchens and bathrooms) 2019 1 10 3.47 3 1.5 1
    Table 2
    Table 2. Description of binary household-level variables and descriptive statistics using the baseline data from the 2019 survey. Dependent variables for urban agriculture engagement are also included from the 2019, 2020, and 2021 surveys.

    Table 2. Description of binary household-level variables and descriptive statistics using the baseline data from the 2019 survey. Dependent variables for urban agriculture engagement are also included from the 2019, 2020, and 2021 surveys.

    Variable type Variable name Description Total (percentage) value = 1 Total (percentage) value = 0 Missing observations
    Dependent Urban agriculture engagement - 2019 Describes whether the household engages in urban agriculture (1 = yes) 276 (42%) 381 (58%) 0
    Dependent Urban agriculture engagement - 2020 Describes whether the household engages in urban agriculture (1 = yes) 337 (51%) 320 (49%) 0
    Dependent Urban agriculture engagement - 2021 Describes whether the household engages in urban agriculture (1=yes) 324 (49%) 332 (50%) 1
    Independent Female-headed household Describes whether the household is female-headed or not (1 = yes) 169 (26%) 488 (74%) 0
    Independent Planned settlement Describes whether the household is situated in a planned or unplanned settlement (1 = planned settlement) 431 (66%) 222 (34%) 4
    Independent Separate house Describes whether the dwelling is a separate house or not (1 = separate house) 515 (78%) 140 (21%) 2
    Independent Rent Describes whether the household is renting the property or not (1 = yes) 180 (27%) 474 (72%) 3
    Independent Electric grid Describes whether the household is connected to the municipal electric grid (1 = yes) 356 (54%) 295 (45%) 6
    Independent Private water source Describes whether the household has access to a private water source on the property (1 = yes) 387 (59%) 270 (41%) 0
    Table 3
    Table 3. Multivariate multiple regression results assessing the relationship between household characteristics with the frequency of days visited in the past two weeks to open-air markets and vendors for the 2019, 2020, and 2021 survey periods. Larger secondary cities are used as the reference category on the control variables for city type.

    Table 3. Multivariate multiple regression results assessing the relationship between household characteristics with the frequency of days visited in the past two weeks to open-air markets and vendors for the 2019, 2020, and 2021 survey periods. Larger secondary cities are used as the reference category on the control variables for city type.

    Dependent variable
    Open air market: 2019 Open air market: 2020 Open air market: 2021 Vendor: 2019 Vendor: 2020 Vendor: 2021
    (1) (2) (3) (4) (5) (6)
    Log of income 0.219 −0.196* −0.053 −0.208* 0.121 −0.002
    (0.151) (0.104) (0.068) (0.107) (0.077) (0.054)
    Female-headed household −0.161 0.107 0.031 0.361 0.002 0.262*
    (0.425) (0.308) (0.205) (0.386) (0.206) (0.158)
    Household size 0.100 −0.044 0.056 0.145** 0.017 0.006
    (0.074) (0.053) (0.037) (0.072) (0.041) (0.027)
    Minutes to bus stop −0.028** −0.014* 0.005 0.006 0.001 0.006
    (0.014) (0.008) (0.006) (0.011) (0.008) (0.004)
    Rent 0.170 0.195 −0.008 0.168 −0.141 0.159
    (0.434) (0.291) (0.212) (0.390) (0.210) (0.155)
    Smaller urban areas 3.526*** −0.869* 1.216*** 1.614** −0.056 0.714***
    (0.763) (0.521) (0.365) (0.766) (0.511) (0.228)
    Remote mid-sized urban areas 1.613*** −0.378 0.411* −0.945** 0.482** −0.015
    (0.499) (0.309) (0.238) (0.407) (0.245) (0.170)
    Connected mid-sized urban areas −0.838* −0.194 1.334*** −0.492 −0.154 0.328*
    (0.431) (0.326) (0.230) (0.360) (0.224) (0.179)
    Constant 4.752*** 6.266*** 3.567*** 3.096*** 0.982 1.312***
    (1.187) (0.824) (0.546) (0.971) (0.612) (0.413)
    Observations 646 642 647 610 611 608
    R2 0.088 0.018 0.064 0.045 0.015 0.024
    Adjusted R2 0.077 0.005 0.052 0.033 0.002 0.011
    Residual std. error 4.662 (df = 637) 3.194 (df = 633) 2.348 (df = 638) 3.868 (df = 601) 2.374 (df = 602) 1.683 (df = 599)
    F statistic 7.694*** (df = 8; 637) 1.424 (df = 8; 633) 5.458*** (df = 8; 638) 3.580*** (df = 8; 601) 1.149 (df = 8; 602) 1.879* (df = 8; 599)
    Note: * p < 0.1; ** p < 0.05; *** p <0.01.
    Table 4
    Table 4. Multivariate multiple regression results assessing the relationship between household characteristics with the frequency of days visited in the past two weeks to local shops and supermarkets for the 2019, 2020, and 2021 survey periods. Larger secondary cities are used as the reference category on the control variables for city type.

    Table 4. Multivariate multiple regression results assessing the relationship between household characteristics with the frequency of days visited in the past two weeks to local shops and supermarkets for the 2019, 2020, and 2021 survey periods. Larger secondary cities are used as the reference category on the control variables for city type.

    Dependent variable
    Local shop: 2019 Local shop: 2020 Local shop: 2021 Supermarket: 2019 Supermarket: 2020 Supermarket: 2021
    (1) (2) (3) (4) (5) (6)
    Log of income 0.396*** 0.183*** 0.114* 0.151 0.154*** 0.096***
    (0.126) (0.064) (0.064) (0.109) (0.051) (0.019)
    Female-headed household −0.024 0.030 0.133 0.104 −0.061 −0.031
    (0.316) (0.201) (0.201) (0.174) (0.116) (0.064)
    Household size −0.134*** −0.019 −0.0001 −0.029 −0.024* 0.010
    (0.044) (0.035) (0.035) (0.020) (0.014) (0.011)
    Minutes to bus stop −0.025** 0.004 0.002 0.008 −0.003 −0.001
    (0.010) (0.007) (0.007) (0.005) (0.002) (0.002)
    Rent −0.567* −0.195 −0.131 −0.062 0.009 0.018
    (0.304) (0.214) (0.214) (0.133) (0.104) (0.068)
    Smaller urban areas 0.253 0.198 1.014** −0.433 −0.138 0.417
    (0.599) (0.417) (0.417) (0.326) (0.426) (0.266)
    Remote mid-sized urban areas 0.005 0.875*** −0.298 −0.846*** −0.459*** −0.342***
    (0.346) (0.301) (0.301) (0.139) (0.093) (0.082)
    Connected mid-sized urban areas −0.661** −0.048 0.153 −0.962*** −0.543*** −0.325***
    (0.303) (0.182) (0.182) (0.152) (0.076) (0.066)
    Constant 1.504 0.407 0.584 −0.038 −0.135 −0.121
    (0.976) (0.544) (0.544) (0.736) (0.329) (0.149)
    Observations 624 583 585 606 550 515
    R2 0.059 0.040 0.075 0.098 0.106 0.105
    Adjusted R2 0.046 0.026 0.063 0.086 0.093 0.091
    Residual std. error 3.320 (df = 615) 2.109 (df = 574) 1.218 (df = 576) 1.496 (df = 597) 0.986 (df = 541) 0.667 (df = 506)
    F statistic 4.782***
    (df = 8; 615)
    2.972***
    (df = 8; 574)
    5.874***
    (df = 8; 576)
    8.092***
    (df = 8; 597)
    8.000***
    (df = 8; 541)
    7.403***
    (df = 8; 506)
    Note: * p < 0.1; ** p < 0.05; *** p < 0.01.
    Table 5
    Table 5. Binary logistic regression results assessing the relationship between household characteristic and engagement in urban agriculture for the 2019, 2020, and 2021 survey periods. Larger secondary cities are used as the reference category on the control variables for city type.

    Table 5. Binary logistic regression results assessing the relationship between household characteristic and engagement in urban agriculture for the 2019, 2020, and 2021 survey periods. Larger secondary cities are used as the reference category on the control variables for city type.

    Dependent variable
    Urban Ag - 2019 (1) Urban Ag - 2020 (2) Urban Ag - 2021 (3)
    Coefficient
    (robust SE)
    Odds ratio
    (confidence interval)
    Coefficient
    (robust SE)
    Odds ratio
    (confidence interval)
    Coefficient
    (robust SE)
    Odds ratio
    (confidence interval)
    Log of income −0.009 0.991 0.196*** 1.216 0.038 1.039
    (0.070) (0.862, 1.140) (0.072) (1.057, 1.407) (0.070) (0.908, 1.189)
    Female-headed household 0.085 1.089 0.109 1.020 −0.197 0.821
    (0.195) (0.735, 1.610) (0.196) (0.757, 1.646) (0.192) (0.563, 1.196)
    Household size 0.020 1.020 0.020 1.020 −0.029 0.972
    (0.036) (0.950, 1.096) (0.036) (0.951, 1.094) (0.035) (0.907, 1.040)
    Planned settlement −0.534** 0.586 0.076 1.079 −0.008 0.993
    (0.209) (0.386, 0.886) (0.203) (0.721, 1.615) (0.197) (0.673, 1.464)
    Distance to bus stop −0.009 0.991 0.008 1.008 0.003 1.003
    (0.006) (0.980, 1.003) (0.006) (0.996, 1.019) (0.006) (0.992, 1.014)
    Separate house −0.071 0.931 0.182 1.200 −0.070 0.932
    (0.237) (0.592, 1.471) (0.233) (0.771, 1.870) (0.217) (0.606, 1.433)
    Number of rooms 0.172** 1.188 0.259*** 1.296 0.130* 1.139
    (0.076) (1.036, 1.365) (0.073) (1.130, 1.493) (0.066) (0.999, 1.301)
    Rent −0.413** 0.662 0.156 1.169 −0.426** 0.653
    (0.210) (0.433, 1.004) (0.206) (0.781, 1.757) (0.205) (0.439, 0.968)
    Electric grid −0.177 0.838 −0.629*** 0.533 −0.040 0.961
    (0.198) (0.563, 1.244) (0.199) (0.358, 0.788) (0.191) (0.659, 1.400)
    Private water source 1.026*** 2.790 0.308* 1.360 0.309* 1.361
    (0.194) (1.912, 4.205) (0.187) (0.939, 1.975) (0.182) (0.952, 1.952)
    Smaller urban areas −0.558* 0.573 0.257 1.293 0.197 1.218
    (0.332) (0.283, 1.137) (0.343) (0.661, 2.575) (0.328) (0.631, 2.364)
    Remote mid-sized urban areas −0.952*** 0.386 0.593** 1.810 0.428* 1.534
    (0.249) (0.236, 0.625) (0.241) (1.130, 2.923) (0.233) (0.973, 2.430)
    Connected mid-sized urban areas −0.684*** 0.504 −0.925*** 0.397 −0.620*** 0.538
    (0.219) (0.325, 0.779) (0.224) (0.255, 0.611) (0.218) (0.351, 0.819)
    Constant −0.387 0.679 -2.387*** 0.092 −0.515 0.597
    (0.567) (0.221, 2.082) (0.606) (0.029, 0.284) (0.553) (0.204, 1.744)
    Observations 634 634 633
    Log Likelihood -392.142 -401.550 -420.596
    Akaike inf. crit. 812.284 831.101 869.193
    Note: * p < 0.1; ** p < 0.05; *** p < 0.01.
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    Home > VOLUME 30 > ISSUE 3 > Article 27 Research

    Nurturing forest memory: native bamboo as an assemblage of biocultural keystone species in the southern Andes

    Levaggi, A. J., and J. T. Ibarra. 2025. Nurturing forest memory: native bamboo as an assemblage of biocultural keystone species in the southern Andes. Ecology and Society 30(3):27. https://doi.org/10.5751/ES-16332-300327
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    • Annika J. Levaggicontact author, Annika J. Levaggi
      ECOS (Ecosystem-Complexity-Society) Co-Laboratory, Center for Local Development (CEDEL) & Center for Intercultural and Indigenous Research (CIIR), Villarrica Campus, Pontificia Universidad Católica de Chile, Villarrica, Chile
    • José Tomás IbarraORCIDJosé Tomás Ibarra
      ECOS (Ecosystem-Complexity-Society) Co-Laboratory, Center for Local Development (CEDEL) & Center for Intercultural and Indigenous Research (CIIR), Villarrica Campus, Pontificia Universidad Católica de Chile, Villarrica, Chile; Department of Ecosystems and Environment, Faculty of Agriculture and Natural Systems (FASN) & Center of Applied Ecology and Sustainability (CAPES), Pontificia Universidad Católica de Chile; Cape Horn International Center for Global Change Studies and Biocultural Conservation (CHIC), Universidad de Magallanes, Chile

    The following is the established format for referencing this article:

    Levaggi, A. J., and J. T. Ibarra. 2025. Nurturing forest memory: native bamboo as an assemblage of biocultural keystone species in the southern Andes. Ecology and Society 30(3):27.

    https://doi.org/10.5751/ES-16332-300327

  • Introduction
  • Methods
  • Results
  • Discussion
  • Conclusion
  • Author Contributions
  • Acknowledgments
  • Data Availability
  • Literature Cited
  • biocultural memory; Chusquea culeou; Chusquea quila; forest management; traditional ecological knowledge
    Nurturing forest memory: native bamboo as an assemblage of biocultural keystone species in the southern Andes
    Copyright © by the author(s). Published here under license by The Resilience Alliance. This article is under a Creative Commons Attribution 4.0 International License. You may share and adapt the work provided the original author and source are credited, you indicate whether any changes were made, and you include a link to the license. ES-2025-16332.pdf
    Research

    ABSTRACT

    Presently, with the acceleration of climate change and rural land development, foraging spaces remain increasingly under threat. In Andean temperate forests of southern Chile, these challenges, coupled with ongoing legacies of colonization, threaten the biocultural memory of an assemblage of foundational understory species, the Chusquea spp. Both the commonly named species kila (Chusquea quila) and koliwe (Chusquea culeou) stand out for their ecological importance and, moreover, for their historical usage and significance among Mapuche and campesino communities. To better understand the biocultural importance of the Chusquea spp., we implemented a biocultural keystone species assessment among Mapuche and campesino communities. Moreover, drawing from community-based participatory frameworks, we collaborated with local foragers to synthesize recommendations for best management practices and develop guidelines to identify high-quality harvestable Chusquea spp. To conduct the biocultural keystone species assessment and synthesize management recommendations, we carried out participant observation, informal interviews, and snowball sampling, and conducted ethnographic interviews and fieldwork assessments with 16 expert foragers across the Mallolafken watershed in the La Araucanía region, southern Andes of Chile. Our results identified the Chusquea spp. as an assemblage of biocultural keystone species, with 62 household uses, critical contributions to food security, ceremonial significance, and cultural roles as a messenger, protector, and companion. Consultation with foragers also determined harvesting guidelines in accordance with use type based principally on variations in (1) color, (2) diameter, and (3) leaf abundance. While few foragers actively manage Chusquea spp. aside from using animal grazing to prune and control growth, some foragers shared techniques for reproducing stands. The lack of salient Traditional Ecological Knowledge related to Chusquea spp. management reflects their threatened biocultural memory. Future research coupled with community outreach regarding Chusquea spp. management is needed to support foraging practices and forest conservation efforts in the region.

    INTRODUCTION

    In recognizing the interconnectedness of social and ecological systems, socio-ecology asks us not only to consider how social injustices have been historically entangled with ecological degradation, but also how processes of repair might similarly go hand in hand (Society for Ecological Restoration 2004, Artelle et al. 2019, Berkes 2021, Lucero et al. 2023). Among practices of repair, nurturing Traditional Ecological Knowledge (TEK) has gained traction as a promising pathway toward ecological regeneration and cultural revitalization (Berkes et al. 2000, Toledo 2002, Turner et al. 2011, Nelson 2014). TEK embraces not only a set of information but the accompanying practices and beliefs that are generationally honed and adaptive to ever-changing social-ecological contexts (Berkes et al. 2000, Toledo and Barrera-Bassols 2008). TEK encompasses the dynamic between a (1) “corpus” of situated biological knowledge (identification, habitat, distribution, seasonality, etc.) and (2) “praxis,” or set of practices (tools, techniques, monitoring, management, etc.) which are embedded within a (3) cosmos, or the cultural context that outlines the use norms and greater worldviews that shape species associations and perceptions (Jacques-Coper et al. 2019). Biocultural memory refers to the process by which experiences, beyond just those of individuals, are gathered and passed down over generations to form a collective cognizance that helps communities adapt to variable social-ecological conditions (Nazarea 2006, Maffi and Dilts 2014). In this way, TEK has been considered a form of biocultural memory (Jacques-Coper et al. 2019). Both TEK and biocultural memory can play critical roles in increasing resilience in the wake of the present social-ecological crisis (Barthel et al. 2010, Gómez-Baggethun et al. 2013a, Turner 2014, Robinson et al. 2021, Ibarra et al. 2024a).

    Certain species are particularly pertinent to nurturing biocultural memory. A species’ importance can be reflected in its presence within cultural spheres of language, art, religion, technology, and so forth (Ibarra et al. 2012). Such species include charismatic megafauna like the grizzly bear (Ursus arctos horribilis), which takes center stage in ceremonies, pastimes, and stories among Indigenous communities along coastal British Columbia (Clark et al. 2021), and foraged food staples like pewen seeds (Araucaria araucana) for the Mapuche Pewenche people of the Andes (Herrmann 2005, Ibarra et al. 2022). In the land-based cultures of many Indigenous peoples, a species’ significance is also extended in terms of its ecological roles, such as in water filtration or soil regeneration (Rozzi et al. 2008, Van Horn et al. 2021, Ojeda et al. 2022). For example, the Lakota revere buffalo (Bison bison) not only within cultural domains but also for their ecological contributions to Great Plains ecosystems (Knapp et al. 1999, Patel and Grey 2014). Notably, species that hold greater significance in both cultural and ecological domains may be denoted as biocultural keystone species (Ibarra et al. 2012). This term is in line with the natural sciences concept of “ecological keystone species”, developed by Paine (1969) to distinguish species with an overwhelming influence over the well-being of whole ecosystems and the later metaphorization by the social sciences that coined “cultural keystone species” (CKS) to acknowledge species that profoundly shape social groups’ well-being or worldviews (Cristancho and Vining 2004, Garibaldi and Turner 2004, Ellen 2006). Over the last decade, numerous research studies have used the biocultural keystone species framework to capture the entangled social and ecological importance of species like the Andean Condor (Vultur gryphus) within Aymara society, and the black ash (Fraxinus nigra) among Wabanaki tribes, as well as in the form of assemblages such as medicinal plants within mountain communities in the Southern Alps (Costanza et al. 2017, Jacques-Coper et al. 2019, Petelka et al. 2022).

    Some studies have explored how changing social-ecological conditions can impact local livelihoods by reducing populations of biocultural keystone species (Costanza et al. 2017, Uprety et al. 2017) or eroding popular reverence for them (Jacques-Coper et al. 2019). Other studies have used the biocultural keystone species concept to identify critical species from a larger set of candidates (Tardío and Pardo-de-Santayana 2008, Thomas et al. 2009, Kazancı et al. 2023). Oftentimes, such work has become associated with flagging focal species to support conservation and restoration work (Garibaldi and Turner 2004, Garibaldi 2009, McKemey et al. 2020). Importantly, the biocultural keystone species concept has been critiqued for its essentializing tendencies that overlook the interactions within assemblages of multiple species (Cottee-Jones and Whittaker 2012, Ogden et al. 2013, Aisher and Damodaran 2016). Hence, in this study, we strive to understand not only how communities in the southern Andes use and manage native bamboo, but also how their lives have been duly shaped by the Chusquea spp. (Tsing 2015, Harraway 2016). Moreover, most biocultural keystone species assessments weigh their arguments in favor of either ecological or cultural contributions and often use qualitative approaches to describing cultural phenomena (Guerrero-Gatica and Achondo 2022). Here, we offer a model for how transdisciplinary collaborations coupled with a quantitative cultural assessment can offer new modes for conceptualizing biocultural keystone species.

    In the southern Chilean Andes, the native bamboo species, the kila (Chusquea quila) and koliwe (C. culeou), represent a potential pathway to nurturing, both ecologically and culturally, some areas of Andean temperate ecosystems and the Indigenous Mapuche and campesino communities whose livelihoods are greatly associated with them. The kila and koliwe are the most common species within an assemblage of bamboo species found in south-central Chile (37-43º S) (Fig. 1). These Chusquea species are characterized largely by their dominance among the understories of temperate Andean forests, between the elevations of 200 and 1000 m (Rojas et al. 2011). As pioneer species, their prevalence is often considered an indicator of deforestation, forest degradation, or previous burning (Veblen 1982). However, their regenerative qualities have been found to play critical roles in enhancing soil stability, biodiversity conservation, and nutrient cycling (Altamirano et al. 2012, Caviedes and Ibarra 2017, Concha et al. 2023). The kila, known by its common name in mapudungun (Mapuche language) as the kila or kilautre, grows primarily between 200 and 700 m elevation and is distinguished by its branching form, which allows it to climb adjacent trees (Veblen 1982). The kila’s ability to produce new branches allows it to grow in heavily shaded conditions and expand rapidly. Between 700 and 1000 m above sea level, the dominant bamboo species becomes the koliwe (colihue or coligüe) or, in mapudungun, the coles or rëngi (Veblen 1982, Ibarra et al. 2018). The koliwe is distinguished by its vertical growth form with stocks that form groupings up to 3 m in diameter (Veblen 1982). These bamboo species have been associated with 58 wildlife species (three reptiles, six amphibians, 20 mammals, and 29 birds), providing food resources, refuge, and nesting opportunities for them (Ibarra et al. 2018). Beyond their ecological role, these bamboo species have long since been embedded in the biocultural memory of the Mapuche communities belonging to Wallmapu (ancestral Mapuche territory). Historically, native bamboo was fashioned into spears and used to construct mazes in the successful defense of Wallmapu against Spanish colonization (González Cangas and González 2006). Both species hold ceremonial significance, and a number of studies have recorded their various uses from construction to artisan works, as well as for fodder and canned food supplies (González Cangas and González 2006, Barreau 2014, Whitman et al. 2014, Cordero et al. 2022). The Chusquea quila, in particular, has been found to have remarkably high nutritional value as animal forage (Venegas 2023).

    Presently, native Andean temperate forests are facing increasing threats due to accelerations in climate change as well as ongoing histories of forestry expansion, intensive agricultural settlement, and suburbanization of wildlands (Lara et al. 1996, Armesto et al. 2001, Herrmann 2005, Barreau et al. 2019). As people (che) of the land (mapu), the resilience of Mapuche culture is directly tied to the health of native forests (Rozzi et al. 2008) and thus has been greatly impacted by centuries of land grabbing, assimilation, and displacement (Bengoa 2003, Coña and de Moesbach 2010, Montalba and Stephens 2014). More recently, changing social-ecological processes have also affected campesino communities. Many campesinos settled in the territory after receiving land claims during the 19th century State-sponsored Pacificación de La Araucanía campaign, and since have lived for generations as small-scale agriculturalists (Bengoa 2000). As such, they hold in-depth and seasoned knowledge of the forests. Today, many campesinos are being parceled out of their properties by rural gentrification (Marchant Santiago 2017, Monterrubio-Solís et al. 2023).

    Given the changing social-ecological landscape of the region, and building from previous research that has demonstrated Chusquea spp.’ critical role in forest ecological structure and dynamics (Veblen 1982, Caviedes and Ibarra 2017, Ibarra et al. 2018), it is important to understand the biocultural role and TEK associated with native bamboo to guide future forest management decisions. Hence, we first aim to evaluate the extent to which we can consider native bamboo as an assemblage of biocultural keystone species within campesino and Mapuche communities in the southern Andes. Second, we present an overview of current TEK and assesses the state of biocultural memory. To do so, we conducted an ethnographic study that accessed native bamboo along the criteria of the cultural keystone species concept (Garibaldi and Turner 2004). Moreover, we relied on community-based participatory frameworks (Méndez et al. 2017, Rossier 2019, Sowerwine et al. 2019, Evans et al. 2022, Ibarra et al. 2023) to guide the research goals and redistribution of results.

    METHODS

    Study area

    This study was conducted in the watershed of Lake Mallolafken (or Villarrica), spanning the municipalities of Villarrica, Pucón, and Curarrehue, in the Andean zone of the La Araucanía region of southern Chile (39ºS). The region is characterized by a temperate climate with a short dry season (< 4 months). Over the last decade, the mean annual temperature has been 12°C, with temperatures varying from 0.8 to 28°C, and a mean annual precipitation of 2143 mm. The area is shaped by volcanic and mountainous topography, with vegetation dominated by Nothofagus obliqua at lower elevations (200–1000 m) and mixed deciduous Nothofagus pumilio and the conifer Araucaria araucana at higher elevations (1000–1500 m) (Gajardo 1995). These native temperate forests funnel into valleys and extend down to rivers and lakes, where most settlement and small-scale agricultural activities are contained. The aforementioned municipal districts are within Wallmapu, the ancestral homelands of the Mapuche people (Fig. 2).

    Fieldwork

    We used a community-based participatory approach and relied principally on ethnographic techniques over the course of nine months of fieldwork, between March and November 2023, in the Mallolafken watershed. The first stage of the work consisted of obtaining free and informed consent from interviewees, building relationships with local foragers, and being introduced to their networks of fellow foragers and related community groups. Participant observation took place during community events, including workshops, community work days or mingas, seed exchange gatherings or trafkintu, and foraging sessions. During participant observation, a series of 50 informal interviews were conducted with relevant local actors (Charmaz 2006, Kovach 2009). They represented both campesino and Mapuche residents of the Mallolafken watershed who shared perspectives principally from personal experience managing and using the Chusquea species on their lands. These actors did not claim extensive bamboo foraging knowledge; thus, their perspectives were understood as providing a more representative picture of the present cultural salience and biocultural memory of bamboo use. We either asked interviewees about specific and often context-relevant topics (i.e., harvesting techniques and edible preparation, while collecting bamboo shoots) or provided open-ended discussion opportunities to gain general insights into biocultural memory. Furthermore, 16 in-depth, semi-structured interviews were conducted with expert foragers. These key local actors were identified by successive referral sampling (Atkinson and Flint 2001, Bernard 2011, Voicu and Babonea 2011). Of the expert foragers who participated in these interviews, 40% identified as Mapuche; 60% identified as Campesino. The interviewees’ ages ranged from 39 to 79 years, with a medium age of 56 years, and 70% had a lifetime of bamboo harvesting experience; overall, interviewees averaged 55 years of experience harvesting bamboo. All interviewees harvested bamboo from their personal property or that of adjacent neighbors. Their foraging areas were located in the valleys and foothills, between 250 and 1000 m, where native bamboo grew in both cleared pasture and the understory of forested tracks, particularly along streams. There was an equal ratio of male to female foragers, who ranged in profession and educational background: most had completed up to primary education and worked in land-based trades. The interviewees varied in their principal use of bamboo, given their diverse backgrounds as gardeners, ranchers, weavers, carpenters, traditional healers, artisans, and chefs.

    In our formal interviews, we asked about native bamboo according to each component of a cultural keystone species outlined by Garibaldi and Turner (2004). We included questions tailored to each of the six CKS criteria to identify (1) uses and frequencies of use, (2) ethnotaxonomic diversity and nomenclature, (3) associated folklore, spirituality, and ceremonial roles, (4) social reputation and cultural salience of use and symbolism, (5) irreplaceability, and (6) frequency and value of trade (Table 1). Open-ended discussion points, such as “What does the kila/koliwe mean to you?” and “What significance, if any, does the kila/koliwe hold for you?”, were also included to address the potential limitations and inherent subjectivity of using solely CKS designations to understand the cultural importance of Chusquea spp.

    Furthermore, we asked interviewees about harvesting practices, species management, and aspects of local biocultural memory associated with bamboo to further broaden our evaluation of the Chusquea spp. beyond the CKS indices. Weather permitting, interviews were accompanied by a walk to assist in harvesting and/or review the quality and growth available within participants’ foraging areas. The total interview time with each interviewee ranged from 3 to 6 hours. Additional written notes were taken during each interview and were followed up with a detailed memo, including follow-up questions to address during either supplementary visits or a phone call.

    Audio recordings were transcribed and analyzed using a priori codes related to each of the six CKS criteria, as well as with open coding to allow emergent themes to arise (Strauss and Corbin 1998). Responses were compared across interviewees and then across existing literature to identify areas of agreement and disagreement, as well as unique responses. Foraging metrics were deduced by using inductive coding, were compared across interviewees, and were reviewed during follow-up conversations (Chandra and Shang 2019). Relevant ethnographic and ethnobotanical literature was also searched for references to Chusquea spp. harvesting, management, and cultural importance (González Cangas and González 2006, Campos et al. 2010, Cordero et al. 2022, Hilger and Mondloch 2021).

    RESULTS

    People and bamboo in the southern Andes: an assemblage of biocultural keystone species?

    Chusquea spp. use

    “The kila is everything. It’s gold in the countryside.” The words of this Mapuche weaver reflected the sentiments of many Indigenous and campesino foragers local to the Mallolafken watershed who harvest bamboo for different purposes. While popular reverence for Chusquea spp. has largely declined, drawing controversy for their association with rodent outbreaks and often confused as non-native species, rural use of native bamboo promotes an alternative appreciation for its diverse offerings. Among campesinos and Mapuche foragers in the Mallolafken watershed, we found native bamboo remains a critical, though waning, resource that supports several aspects of daily life in rural areas.

    We identified 62 current household uses of Chusquea spp. (Fig. 3). The uses can be broadly grouped in terms of (1) home goods, (2) food and kitchen, (3) artisanry, (4) home gardening (5) carpentry, (6) spirituality, (7) ranching, (8) construction, and (9) historical uses (Table 2). Each participant listed, on average, 18 personal uses of bamboo, plus an average of four additional uses they knew of but did not personally practice. Notably, unlike our overall total, this measurement was based on classification only to a general level; hence, “furniture” was counted as one use type, although several participants presented multiple examples of bamboo furniture, such as chairs, benches, tables, and bed frames. Additional uses were determined through participant observation and follow-up discussion.

    While bamboo does not constitute a caloric staple in the Mapuche or campesino diet, it may still be regarded as important to their food security. Historically, Chusquea spp. seeds were collected and cooked similarly to rice or were milled into grain (Cordero et al. 2022). Today, shoots are still collected in the spring and are consumed in several forms, including boiled, roasted, or canned to increase winter food supplies. The creativity in cooking Chusquea spp. was described to come from periods of scarcity, when communities turned to the plant, which is otherwise reserved as animal forage, to meet their own nutritional needs.

    The Chusquea spp. also stand out for their technological support across home gardening and ranching activities. Their applications include animal fencing, crop trellising, and greenhouse frames. Koliwe, in particular, is also commonly crafted into traditional agricultural tools, such as polleras (bamboo fences that impede grown chickens from eating chick feed), zarrandas (bamboo-slatted racks used to smoke/dry meat and ferment cheese), and llepüs (flat woven baskets used to winnow grains). Particularly long bamboo stocks are used for fruit picking and springtime foraging of highly coveted digüeñe (Cyttaria espinosae). Additionally, ranchers often reserve rangeland sectors with abundant bamboo growth for chicken egg laying and winter grazing, as well as for collecting foliage for sheep pen bedding. While the Chusquea spp. might not be a remarkable caloric or nutritive food source in Mapuche or campesino households, their profound persistence within farming, ranching, foraging, and fishing activities alike begins to underscore their keystone role within daily life.

    For centuries, Mapuche communities have relied on Chusquea spp. to construct their rukas (traditional houses) because they add rigidity to walls and roofing (Whitman et al. 2014). In recent years, locals have shown increased interest in exploring bioconstruction techniques and practices for building with Chusquea spp. While the bamboo stocks typically reach a diameter of only 2–3 cm, unlike Polynesian varieties, they are solid and thus can be grouped to meet structural needs (Whitman et al. 2014). The use of bioconstruction techniques was less common among the campesino and Mapuche foragers we interviewed: simple roofs, fences, and furniture were the most frequently cited construction applications. However, according to participants, native bamboo use (especially of koliwe) in sustainable design represents a compelling pathway to revitalizing the species’ importance.

    Due to their local abundance, affordability, and relative durability, Chusquea spp. fill the role of most household staples. Chusquea spp. are made into everyday essentials, such as utensils, are pruned and dried for kindling, and are crafted into torches, which was especially common before electricity arrived in the countryside. Moreover, Chusquea spp. are also a primary material for furniture and carpentry needs. Therein, Chusquea spp. remain central to several artisan traditions. In the territory, long stocks of Chusquea spp. are used as weaving material in traditional lampworking and basketry. Mapuche weavers use koliwe to build witrals (looms), and craft tononwe and rangiñelwe, tools that create tension and hold the yarn. Some weavers reported using koliwe as a natural wool dye. Mapuche artisans also craft instruments, children’s toys, and sports equipment from native bamboo.

    Ethnotaxonomy

    All interviewees were able to list the two most common local bamboo varieties: Chusquea culeou and C. quila. Some interviewees lacked the scientific verbiage to characterize them as distinct species, referring to C. quila as the “older” version or “cousin” of C. culeou. The same naming systems we identified were consistent among interviewees and with the literature: C. culeou was referred to as koliwe, C. quila as kila or kilautre, and bamboo stands as kilatral or koligual. We also observed examples of specialized terminology related to tools and uses of bamboo, as described in the Chusquea spp. use section. Here, spelling varied greatly, a possible combination of the interviewees’ limited formal educational levels and the oral-based traditions of Mapuche culture (Barreau et al. 2016).

    Socio-cosmology of native bamboo as a messenger, protector, and companion

    When asked about the symbolism of Chusquea spp., foragers unanimously brought up the belief that bamboo flowering served as a bad omen for a period of forthcoming scarcity. Today, many associate such scarcity with ratadas—outbreaks in rodent populations due to increased volume of food supplies from the abundant seed stock—that often get into household food supplies. However, the omen’s mysticism is not all lost on residents; many recounted seeing flowering bamboo before the COVID-19 pandemic. Notably, the perspectives of Mapuche foragers offered a further understanding of flowering episodes, explaining the Chusquea spp.’ role as a messenger.

    Many Mapuche foragers shared that the bamboo flowering represented a call to prepare for elongated periods of hardship. One forager told the story of a volcanic eruption, following a flowering episode, that covered his property in several centimeters of ash. While he recounted the associated hardships, he also remarked that the nutrients from the ash eventually helped fertilize his pasture and contributed to future years of abundance. Similar stories brought depth to the understanding of native bamboo beyond a totem for scarcity. Another Mapuche forager traced the omen back to the first wave of colonization, sharing the legend that just before contact, the bamboo flowered in Wallmapu, and subsequently caused the first ratada. At the time, the appearance of non-native rodents served as a profound warning and call to action for the Mapuche Nation. During that time, bamboo was revered as a protector, as it was said, “As long as there is koliwe on our land, as long as there is koliwe to make our spears, the huinca, the invader, will not pass.” Huinca, a Mapuche term, refers to non-Mapuche white Chileans and Argentines.

    The image of the Chusquea spp. as a protector, on one hand, can be attributed to their role in the defense of Wallmapu. Beyond issuing warning signals or simply serving as a backbone of many households, bamboo was fashioned into weaponry, including spears, and was used to create mazes through the forest (González Cangas and González 2006). But, in addition to their practical contributions, Chusquea spp. are considered to be endowed with spiritual qualities of protection and companionship. As one forager remarked, “The koliwe is very important in our culture. It’s very wise, like a brother. It’s at your service. It takes care of you, heals you, [and] accompanies you.” For these reasons, Chusquea spp. stocks are used as hiking sticks, and their leaves are used to lay beds where machis’, traditional Mapuche healers, treat patients.

    Koliwe’s vertical form, in particular, is said to connect wenu mapu (the land of above or the “heavens”) with wallmapu (the land and name of the Mapuche territory). Many foragers referred to its spirituality and symbolism as a messenger, protector, and companion. Among Mapuche culture, dreams play a powerful role in transmitting wisdom (Barreau 2014). Burning koliwe and placing its coals under a person’s pillow was said to help them remember dreams, and the appearance of koliwe in dreams signals an important message is being communicated. Given their spirituality, Chusquea spp. are included in rewes (Mapuche altars) and in several ceremonial elements, such as pipes, flag holders, and the trutruka (a trumpet-like wind instrument). Machis’ also use Chusquea spp. for their medicinal properties. One interviewee explained that the liquid derived from stocks, captured when heating stocks over a flame, is used to treat muscle pain and soreness. Further archival research showed that Chusquea spp. are also used to treat menopause symptoms and sexual impotence, and to relieve molar pain, and are used as a natural contra-contraceptive (Cordero et al. 2022).

    Cultural persistence

    Despite their profound versatility, cultural importance, and ecological role among temperate forests, outside of Mapuche and campesino communities the Chusquea spp.’ likeness remains tenuous. During our interviews, foragers were asked about their community’s perception of the species and their broader social reputation. There was consistent agreement that foraging practices and cultural knowledge are being lost. Foragers remarked that very few community members remembered the intricacies of harvesting, and even fewer remembered the craftsmanship of use. While internal community knowledge networks were perceived as fragile, foragers unanimously remarked that those who had left the countryside to live in urban centers had also left behind Chusquea spp. foraging practices. Among conversations with non-foragers, it was not uncommon for them to refer to Chusquea spp. as either invasive or a weed. Most commonly, foragers attributed the decline in use and knowledge to changes in education, the rural youth exodus away from the countryside, and the increased privatization of land by “lifestyle” migrants. Foragers were in consensus that there is a lack of information on the importance, use, and conservation of native bamboo. Such missing resources were often attributed to the behaviors of the aforementioned “lifestyle” migrants, who were described as focusing their attention, upon purchasing land, on removing native bamboo to “clean up” their properties. Given the community-based framework of our project, we worked with foragers to create an accessible guide that included information about the ecological role, distinct uses, detailed harvesting guidelines, and basic management practices for Chusquea spp. (Fig. 4). The guide was shared with project participants, a network of local school teachers, and other inhabitants with the intention of improving education about native bamboo.

    Replaceability

    Given the breadth of use types of Chusquea spp., we did not identify other native species that rivaled their versatility. However, we did observe larger social-ecological shifts in the territory that are impacting the use and perception of bamboo in the area. Notably, the use of exotic species, namely pine (Pinus spp.), that were introduced appeared to be preferred over the use of bamboo in certain historical construction forms. For example, one forager noted that she prefers building her greenhouses from lumber because the short-roofed form of bamboo greenhouses does not provide her with sufficient planting space. When it came to the consumption of shoots, some foragers suggested that gathering shoots is less popular, given the association of wild edibles with poverty and their replacement with industrial commodities. Cruz-García (2006) found that especially among younger generations, increased consumption of market foods in place of wild edibles has become a status symbol. In other cases, preference changes were driven by questions of accessibility. One family noted that since the last flowering event, they have not been able to find harvest-quality bamboo, while others described having to cross into their neighbor's property to forage. The question of forest accessibility has been well documented in the region, as privatization and parcelization represent leading barriers to foraging wild resources (Barreau 2014, Barreau et al. 2016).

    Pertinence to trade and economic opportunities

    We recorded several instances of trade pertaining to the artisanal traditions associated with Chusquea spp., particularly their applications in food preparation, craft, carpentry, and construction. However, bamboo craft was largely contained to small-scale artisanal practices, while construction with bamboo was often linked to its relative affordability. Some interviewees also mentioned trading raw materials between neighbors or at larger export scales; however, such activities appeared uncommon due to the species’ abundance in the region. Hence, the Chusquea spp., while implicated in trade, did not appear to have a high economic value.

    Traditional Ecological Knowledge: foraging native bamboo

    Traditional Ecological Knowledge is a practice of embodied knowledge rooted in a particular place (Ingold 2012). With Mapuche pedagogy, transmission of TEK is oral and in situ, or learned by doing. Likewise, many of the campesino households we interviewed described learning about bamboo foraging through similar processes of accompanying caretakers. However, the erosion of TEK has been recorded as a consequence of rapid social-ecological transformation in the region (Barreau et al. 2016). Hence, as part of understanding the state of the biocultural memory of Chusquea spp., we accompanied foragers and asked them about gathering practices and associated TEK.

    Quality metrics and harvesting considerations

    Foraging Chusquea spp. appeared to be embedded within cultural practices similar to other foraged products. Interviewees explained that they harvest only for specific and predetermined uses, take only small proportions of what is available, ask for permission to harvest, and leave offerings. Foragers shared beliefs about how much to harvest and when—including skipping foraging seasons altogether after mass-flowering events to allow for species regeneration.

    Gathering Chusquea spp. stocks did not appear to be bound to any particular season, like seeds or mushrooms, or by a maturity scale, like berry ripeness or tree age. Rather, every Chusquea spp. stock has a use. Based on our interviews, harvesting Chusquea spp. depends on the intended use and then principally on (1) color, (2) width (stock diameter), (3) flexibility, (4) amount of leaves, (5) stock height, and (6) stock shape. Color was unanimously considered the most reliable indicator of maturity; young stocks have a distinct green tincture that turns yellow with age, and then the stocks become gray, dry, and brittle (Campos et al. 2010). Width was usually classified into three categories. Thin stocks (< 2 cm) are favored for detail-oriented work such as ornamental construction. Medium stocks (~2 cm, which is the most common diameter of a mature stock) are used most frequently for meeting household needs, such as trellising, broom handles, or knitting needles. Thick stocks (> 2 cm) are reserved for structural applications or for uses that require cutting a stock into length-wise segments, such as for basketry or spoon making. Flexibility, which is largely a proxy for age because the lignification process increases rigidity once the stock reaches maturity, refers to the ease with which a stock could be curved or bent. Flexibility is important for certain uses, such as building greenhouses or making fishing rods, which require ductile stocks; however, the opposite is true for applications such as making furniture or roofing. Artisanal practitioners often noted using fire to flex stocks when greater curvature is desired, such as when crafting snowshoes. The amount of leaves was used as a proxy for stock age and flexibility because young stocks retain their culm sheaths until they finish lignification and become rigid (Campos et al. 2010). Height was considered of secondary importance because most plants growing in foraging zones easily reach heights that surpass foragers’ needs. Only in certain cases, such as for basket weaving or fruit picking, did height become a primary factor to consider. Similarly, stock shape was a factor in unique circumstances and referred to whether a stock grew uniformly straight or had natural curvature, such as when a stock grew around a fallen log. The latter case was sought after in particular when foraging for guiños. Notably, harvesting bamboo shoots for consumption followed a more uniform set of guidelines (Table 3). Shoot foraging occurs in the spring, from September until early November. Only shoots that reach ~16 cm tall, have purple leaves, a diameter of at least 1.5 cm, and are still relatively soft when squeezed should be harvested.

    Habitat

    Foragers were asked to characterize the habitat of Chusquea spp. generally, and then comment specifically about light availability, canopy coverage, altitude, water and humidity levels, temperature, grade/aspect, soil type, and species interactions. These metrics were selected because they represent relevant management-dependent variables.

    Generally, foragers identified the habitat of Chusquea spp. with great consistency, naming streambed ravines as the most likely place to encounter harvestable Chusquea spp. Foragers noted that while Chusquea spp. seemed to prefer semi-shaded conditions, it was not uncommon to see the species thriving in open field pastures, which were often reserved by ranchers to maintain accessible forage for animal grazing purposes. When asked specifically about habitat variables, foragers offered a variety of observational analysis. One forager described the soil type by remarking how Chusquea spp. grow on his property from the edge of the forest to the rocky cliffs above his home, and he attributed the plants’ own leaf matter to its ability to grow in diverse soil types. Another forager spoke about associated species by describing how she always finds the “best” and most orange changle (Ramaria flava) below Chusquea spp. groves. Several accounts described Chusquea spp. growing along various aspects, with several foragers remarking that their roots help stabilize soil and prevent erosion.

    Table 4 outlines the foragers’ knowledge about management-relevant habitat variables of Chusquea spp. Notably, remarks about favored conditions became relevant when foragers were asked about management practices, especially when reproducing stands.

    Management considerations

    While many foragers denied managing or knowing of ways to manage native bamboo stands, several described activities that could be considered forest management. The most commonly described practices were pruning and reproduction. While only one forager explicitly named pruning as a management technique, several said that grazing animals naturally kept the bamboo on their property from growing intrusively. Foragers considered pruning by trimming stock ends through animal grazing, and clearing out dry or yellowed stocks for kindling or other uses as a critical active management form. While all foragers maintained close access to foraging areas, between 15 and 300 m from their homes, some described having planted select stands of Chusquea spp. on their property. Bamboo was most commonly planted via seed, rhizome transplant, or stock transplant. The latter was said to be the most successful reproductive method. Foragers affirmed the importance of transplanting stocks in areas according to the aforementioned habitat guidelines for optimal success, and some even noted observing improved growth in stands where they applied mulch and/or compost.

    DISCUSSION

    Our ethnographic research revealed in-depth Traditional Ecological Knowledge associated with the harvest and use of Chusquea spp. as both ancestral and current practices in the southern Andes. Information pertaining to use, harvest, and cultural significance of Chusquea spp. was far more abundant and a matter of greater agreement than management, in terms of either species regeneration or active care. Despite there being a growing community of novice foragers who are sharing uses for native bamboo through woodworking and bioconstruction workshops, and who are experimenting with species management, largely through pruning on personal property, ancestral practices did not appear as salient biocultural memory.

    Considering the criteria outlined by Garibaldi and Turner (2004), we found that while native bamboo once appeared to be considered an assemblage of biocultural keystone species, today the biocultural memory of the Chusquea spp. remains considerably threatened. Building on previous research that demonstrated the ecological importance of Chusquea spp. (Veblen 1982, Altamirano et al. 2012, Caviedes and Ibarra 2017, Ibarra et al. 2018, Concha et al. 2023), we outlined the cultural significance of the assemblage of species belonging to the Chusquea genus in southern Andean temperate landscapes. Our assessment was based on the versatility and frequency of local bamboo use across pertinent cultural domains, including food production, construction, craftsmanship, and medicine, and more so, reflects Chusquea spp.’ cultural regard through symbolism, storytelling, and spirituality (Table 5). At the same time, we observed a considerable decline in the persistence and memory of use of Chusquea spp. in relationship to cultural change. Other criteria—namely, terminology, level of unique position, and trade opportunities—were also assessed as supportive of a biocultural keystone species (BCKS) designation. We identified several naming schemes and associated terminology, found no other native species capable of fulfilling the breadth of material and/or spiritual roles of native bamboo, and recorded a variety of trade opportunities. Notably, while these three criteria were present, they also appeared particularly impacted by changing social-ecological conditions that have driven local Indigenous languages toward extinction, introduced several non-native species that have begun to displace certain bamboo uses, and increasingly replaced traditional trade systems with commercial markets (Klubock 2014, Barreau 2014, Moya-Santiagos and Quiroga-Curín 2022).

    Notably, the cultural keystone species concept, which we adapted and expanded as the biocultural keystone species concept (Ibarra et al. 2012), has drawn debate for its conceptual ambiguities, lack of standardized evaluation methods, subjectivity of the people evaluating the criteria, and static and essentializing tendencies (Platten and Henfrey 2009, Cottee-Jones and Whittaker 2012, Coe and Gaoue 2020, Petelka et al. 2022). These limitations informed our qualitative and ethnographic approach to capturing narrative-driven knowledge of native bamboo from a diverse set of actors. Likewise, accessing the state of biocultural memory alongside BCKS qualifications allowed for a more dynamic conceptualization of how Andean communities’ relationship with native bamboo has changed over time. While our ethnographic approach also supported our documentation of culturally sensitive TEK, our limited sample size highlights the need for future research that explores more systematic or intergenerational sampling to understand the depth of biocultural erosion. We also recognize that forests are complex adaptive systems (Messier and Puettmann 2011, Parrott and Meyer 2012, Ibarra et al. 2020). And specifically, that in degraded forests, such as where native bamboo thrives, emergent relationships between humans and more-than-humans are particularly adaptable in order to compensate for underlying social-ecological changes (Tsing 2015, Harraway 2016). While our study largely contends with human’s cultural transformations with respect to bamboo, further studies that use transdisciplinary and multispecies lens are needed to better understand how human–bamboo relationships in the southern Andes might have fluctuated across social and ecological timescales and thus how the two might relate in the future to support social-ecological resilience (Ibarra et al. 2024b).

    Previous studies that have identified biocultural keystone species have built cases upon the persistence and memory of use in relationship to cultural change—one of the six criteria forwarded by Garibaldi and Turner (2004). While our study identifies extensive native bamboo use and cosmology today, we also found limited management knowledge about native bamboo and a decline in use beyond rural communities. Similar results have been recorded in CKS assessments of case studies on the Andean condor (Vultur gryphus) and umbuzeiro tree (Spondias tuberosa), which reported diminished popular reverence for those species (Peroni et al. 2013, Jacques-Coper et al. 2019). We understand the general decline in native bamboo use not as a factor against its cultural importance but rather as a product of the changing social-ecological context. Here, the sensitivity of CKS to social-ecological changes represents one of the reasons why they are strategic focal points for conservation work (Garibaldi 2009, Uprety et al. 2017, Winter et al. 2018, Petelka et al. 2022, Axelsson and Franco 2023). Given that CKS are often vulnerable to human impacts at local scales (Moola et al. 2007, Baker 2021) and that their importance can decline concurrently with the cultures that nourish them (Cámara-Leret and Bascompte 2021, Ladle et al. 2023), our assessment of a decline in the Chusquea spp. as a BCKS underscores the importance of nurturing bamboo revitalization among campesino and Mapuche communities as a pathway for fostering both social and ecological resilience.

    In a recent literature review, Mattalia et al. (2024) suggested that the CKS determination may be better conceptualized as a continuum according to gradients of relationship intensity. Within such a dynamic conceptualization of human and more-than-human interactions, Chusquea spp. can be considered an assemblage of biocultural keystone species, at the same time their biocultural memory appears considerably threatened. Despite use and harvesting practices being evidently salient, the fragmenting biocultural memory beyond the countryside raises concerns for greater regard and use of native bamboo. In addition to a reduction in the number of experienced bamboo foragers, threats to biocultural memory were observed via the lack of understanding of how to manage bamboo stands, especially along foraging needs. For example, we recorded few suggestions for how to manage a stand to produce taller or wider stocks. These declines in biocultural memory should be understood within the greater histories of loss of native Andean forest and ongoing legacies of colonization, including land grabbing and assimilation (Bengoa 2003). While the expansion of agriculture and timber industries alongside urbanization have changed the local abundance and distribution of native bamboo, compounding socioeconomic transformations have also interrupted intergenerational cultural exchange, especially when it comes to passing down TEK within Indigenous communities (Coña and de Moesbach 2010, Montalba and Stephens 2014). Within the Mallolafken watershed, the decline of TEK has been linked to the exodus of Indigenous and campesino youth moving away from the countryside because many of them are unable to envision a future within rural economies (Schnettler et al. 2013). Also at play is the hyper-nationalization of education, which excludes TEK from the curriculum (Cruz-García 2006) and interrupts many social dynamics that would otherwise allow for intergenerational knowledge transfer, such as reducing children’s time spent in the home (Krohn and Segrest 2010, Barreau 2014). Thus, efforts to revitalize bamboo TEK may help prevent further cultural loss while also supporting the ecological benefits of Chusquea spp. (Altamirano et al. 2012, Caviedes and Ibarra 2017, Ibarra et al. 2018).

    Mattalia et al.’s (2024) literature review also suggests a CKS evaluation should explicitly acknowledge the reciprocal relationships between sociocultural groups and species. For this reason, we assessed the current TEK associated with native bamboo alongside Garibaldi and Turner’s (2004) criteria—as reciprocity can largely be understood as the stewardship of a CKS and its habitat. However, we also understand stewardship of native bamboo, like any wild resources, in terms of “multispecies” interaction. In an attempt to undo traditions of essentialism within place-based conservation, sociologists derived the multispecies concept to suggest that not only have human communities influenced more than human species but that the reverse is also true (Ogden et al. 2013, Aisher and Damodaran 2016). Previously, Medrano and Rosso (2016) showed how biocultural keystone species can be implicated in these multispecies frameworks by describing how Qom Indigenous ontologies extend emotional and even kinship relationships with the ñandú’s (Rhea americana). In their study, they write, “the [Qom] without the rhea, are not people.” Similar to the ñandú, we might think of how not only have humans influenced Chusquea spp. but that bamboo has also shaped human life in the process of “becoming with” (Haraway 2016). The multispecies framework has often been invoked when considering degraded landscapes to suggest that the construction of multispecies worlds amid disturbance can offer hymns of biocultural hope (Tsing 2015). Famously, Tsing (2015) discussed how matsutake (Tricholoma matsutake) abundance can offer a guide for surviving capitalist ruins. In the southern Andes, the complex relationships between humans and native bamboo species can offer a similar conceptualization of multispecies interactions. If we remember, the Chusquea spp. once played a critical role in the defense of Wallmapu. Elder foragers said that following colonization and the subsequent large-scale disturbance to the native forests, the distribution of Chusquea spp. changed dramatically. According to ancestral accounts, there is less forgeable koliwe (Chusquea culeou) and more sprawling kila (Chusquea quila), which is making some areas of the forest impassable. With the multispecies lens, we might ask how might kila be protecting the forest anew? And, as pioneer species, what lessons might Chusquea spp. offer about thriving amidst ruins? Such questions invoke important alternative ontologies for considering how to nurture biocultural memory while challenging the essentializing tendencies of the biocultural keystone species concept, and in that way, can be important to consider when thinking about native bamboo’s role in conservation.

    The biocultural keystone species has been touted for its potential to support conservation work, particularly to identify species that could serve as strategic focal points for regeneration and/or monitoring (Garibaldi and Turner 2004, Garibaldi 2009, Butler et al. 2012, Costanza et al. 2016, Uprety et al. 2017). It has been suggested that the local interest and sense of place evoked by biocultural keystone species can help promote interest in conservation, while also aligning land management with cultural values. The identification of culturally critical species has been shown to protect Indigenous rights, in particular (Reyes-García et al. 2022). Successful applications can be seen in the case of the black ash in guiding wetland management (Costanza et al. 2017), and with the eastern white pine (Pinus strobus L.) in forest regeneration monitoring (Uprety et al. 2017). The similar social-ecological pertinence of Chusquea spp. suggests it might be a promising pathway for conservation. Foraging wild edibles in Andean forests has been shown to play a role in land stewardship, such as how gathering baskets can impact the distribution of mushroom spores (Barreau et al. 2016). While Chusquea spp. were previously misunderstood to encumber canopy growth (González et al. 2002, Muñoz et al. 2012) and their removal was linked to promoting natural regeneration in degraded forests (Bannister et al. 2024), further studies showed that Chusquea spp.’ dominant post-disturbance growth can enhance understory health (Altamirano et al. 2012, Caviedes and Ibarra 2017, Ibarra et al. 2018). The Chusquea spp. have similar ecological services and cultural relevance as other Latin American bamboo species, such as the Guadua, which has likewise been a proposed focus of land management, given its pertinence among Amazonian tribes (Virtanen et al. 2022). That said, it should not be overlooked that native bamboo has dominated certain forested areas in a way that presents challenges to foragers, either because forage quality is low or forage is difficult to access. A better understanding of culturally relevant management of Chusquea spp. could support forest health alongside foragers’ needs.

    CONCLUSION

    The role and use of Chusquea spp. among campesino and Mapuche communities in the southern Andes supports previous research that suggested the potential of non-timber forest products to be critical biocultural keystone species (Shakelton et al. 2018). However, it duly raises questions about how the understood biocultural values might be incorporated into broader forest management and conservation approaches. Such declining salience regarding native bamboo TEK underscores the importance of future research collaborations with foragers to identify and evaluate possible management strategies. While our study identified salient uses and foraging practices related to Chusquea spp., the little remaining Traditional Ecological Knowledge regarding species management reveals declining biocultural memory. We hope the quality assessment guidelines, habitat considerations, and management best practices can serve as a starting point for future research to strive to better understand how to tend temperate Andean forests to support healthy and high-quality harvestable bamboo for the communities that rely on them.

    RESPONSES TO THIS ARTICLE

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    AUTHOR CONTRIBUTIONS

    Annika Levaggi: Conceptualization, methodology, investigation, formal analysis, writing – original draft, review and editing, visualization, funding acquisition José Tomás Ibarra: Conceptualization, writing – review and editing, supervision

    ACKNOWLEDGMENTS

    This research was conducted as a Fulbright research project of Annika Levaggi. We are grateful to the local foragers, gardeners, campesinos, and artisans for their generosity and contributions to this project. Moreover, we could not have completed this project without the support of the Center for Local Development (CEDEL) and the ECOS (Ecosystem-Complexity-Society) Co-Laboratory. We thank colleagues Rocío Alumna, Magdalena Reyes, and Alexis Catalán Caniulef for their support in introducing AL to foragers in the territory, and Amapola Núñez for her support with mapping and GIS. This work was supported by the Fulbright U.S. Student Program, which is sponsored by the U.S. Department of State and the Chilean Fulbright Commission. Its contents are solely the responsibility of the authors and do not necessarily represent the official views of the Fulbright Program, the Government of the United States, or the Chilean Fulbright Commission. We acknowledge the support from ANID/Fondecyt Regular 1200291, the Center for Intercultural and Indigenous Research–CIIR (ANID/FONDAP 15110006), the Cape Horn International Center–CHIC (ANID PIA/BASAL PFB210018), and the Center of Applied Ecology and Sustainability–CAPES (ANID PIA/BASAL FB0002).

    Use of Artificial Intelligence (AI) and AI-assisted Tools

    AI generative or AI-assisted technology was not used in the process of writing the paper.

    DATA AVAILABILITY

    The data and code that support the findings of this study are available on request from the corresponding author, AL. None of the data and code are publicly available because they contain information that could compromise the privacy of the research participants. Ethical approval for this research study was granted by the Ethics Committee of the Pontificia Universidad Católica de Chile, protocol code 190603004.

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    Corresponding author:
    Annika Levaggi
    ajlevaggi@gmail.com
    Fig. 1
    Fig. 1. The <em>Chusquea quila</em> (left) and <em>Chusquea culeou</em> (right).

    Fig. 1. The Chusquea quila (left) and Chusquea culeou (right).

    Fig. 1
    Fig. 2
    Fig. 2. Location of the study area within the Mallolafken (Villarrica) watershed (39°S 71°W) in the southern Andes of Chile.

    Fig. 2. Location of the study area within the Mallolafken (Villarrica) watershed (39°S 71°W) in the southern Andes of Chile.

    Fig. 2
    Fig. 3
    Fig. 3. Some uses of native bamboo in the southern Andes: (A) greenhouse frame, (B) chair, (C) fishing rod, (D) Mapuche loom, (E) koliwe (<em>Chusquea culeou</em>) shoots, (F) bamboo spoons.

    Fig. 3. Some uses of native bamboo in the southern Andes: (A) greenhouse frame, (B) chair, (C) fishing rod, (D) Mapuche loom, (E) koliwe (Chusquea culeou) shoots, (F) bamboo spoons.

    Fig. 3
    Fig. 4
    Fig. 4. Selected pages from the community manual on native bamboo: (A) cover page, (B) biological morphology, (C) example image of household uses, (D) image of ecological role and associated wildlife species.

    Fig. 4. Selected pages from the community manual on native bamboo: (A) cover page, (B) biological morphology, (C) example image of household uses, (D) image of ecological role and associated wildlife species.

    Fig. 4
    Table 1
    Table 1. Interview questions associated with cultural keystone species (CKS) criteria.

    Table 1. Interview questions associated with cultural keystone species (CKS) criteria.

    CKS criteria Interview questions
    Intensity, type, and multiplicity of use In what ways do you use the Chusquea spp.? Are there other uses that you know of but do not personally practice? How often do you use [use type]? How do you make [use type] from the Chusquea spp.?
    Naming and terminology in a language If you consider the species of [Chusquea spp.] bamboo that grows in this area, how many types would you say there are? What do you call them?
    Are there any other names you use to refer to these plants? Are there any other names you have heard but do not personally use?
    Role in narratives, ceremonies, or symbolism Do you know of any myths, symbols, or histories associated with Chusquea spp. bamboo? What do they say?
    Are you familiar with any ceremonial purposes or spiritual uses of Chusquea spp.?
    Persistence and memory of use in relationship to cultural change How would you describe the general reputation of Chusquea spp. today? Are their many people in your community who use the species or know of its uses? What about beyond your community in Wallmapu at large?
    What is the process of harvesting Chusquea spp.? When harvesting Chusquea spp., what factors tell you a shoot or stock is ready to harvest? And what factors indicate it is of high or low quality? How do you take care of bamboo habitat? Do you ever do anything to help the plant grow better?
    Level of unique position in culture Of the aforementioned uses, are there other plants that might be used in place of the Chusquea spp. bamboo to fulfill the same purposes?
    Opportunities for trade beyond the territory Is the Chusquea spp. ever traded? Today, does there exist relevant commercial value or trade opportunities for bamboo? What about historically? Do you know of any uses for the species distinct from those beyond the Mallolafken watershed?
    Table 2
    Table 2. Use types of native bamboo in the Mallolafken watershed, southern Andes of Chile.

    Table 2. Use types of native bamboo in the Mallolafken watershed, southern Andes of Chile.

    Domain Use Total
    Home goods Kindling, torches, charcoal pens, ink holders, broom handles, chimney cleaners, umbrella holders, curtain rods, drying racks (clothes), hiking sticks, walking canes, crutches 12
    Food/kitchen Raw vegetable shoots, conserves, grain meal, rice-like preparation of seeds, fishing rods, skewers and other utensils, meat smokers, zarrandas (cheese drying racks), cutting boards 10
    Artisanry Lamps, baskets, knitting needles, wool hand spinners (Aspa), natural dyes, carton/paper, kites, guiño (hockey-like sticks used in Mapuche pastime chueka), bicycles, and children’s toys 10
    Home gardening Trellising, fruit pickers, tree tutors, greenhouse frames, llepü (winnow baskets), pollera (chick feed fences), ornamental 7
    Carpentry Tables, chairs, benches, bed frames, hammocks, cribs 6
    Spirituality Trutruka (Mapuche instruments used in ceremony), drum sticks, pipes, flag holders, altar contributions, medicine 6
    Ranching Animal fodder, herding sticks, animal bedding, animal refuges, oxen rings 5
    Construction Roofing, walls, gates, fencing 4
    Historical uses Pica (spears), baby walkers 2
    Total 62
    Table 3
    Table 3. Sample harvesting guidelines of <em>Chusquea</em> spp. bamboo in the southern Andes.

    Table 3. Sample harvesting guidelines of Chusquea spp. bamboo in the southern Andes.

    Chusquea spp. foraging index
    Use type Color
    (purple, green, yellow, black, dry)
    Width
    (thin, medium, thick)
    Flexibility
    (highly, somewhat, none)
    Other considerations
    Furniture Green or yellow Thick for structural components, medium to thin for decorative work None
    Somewhat for decorative work
    Check for burrowing insects
    Garden trellising Yellow or dry Medium None Yellow stocks last 1–3 farming seasons
    Shoot conserve Purple with yellow hues Medium N/A Harvest when still soft, approximately 16 cm tall
    Utensils Yellow Medium to thick None Check for burrowing insects
    Knitting needles Yellow Thin to medium None Stalks should be straight
    Fishing rods Green with yellow hues Thin to medium Somewhat Height should measure just above 1 m
    Basketry Green Thick Very Taller (> 2 m) stocks are preferred
    Table 4
    Table 4. <em>Chusquea</em> spp. habitat variables, according to forager accounts, in the Mallolafken watershed in the southern Andes.

    Table 4. Chusquea spp. habitat variables, according to forager accounts, in the Mallolafken watershed in the southern Andes.

    Variable Forager accounts
    Light availability Most Chusquea spp. prefer semi-shaded conditions; however, it is not uncommon for them to grow in all shade types, including full sun.
    Canopy coverage Most Chusquea spp. will grow below larger trees, although it is not uncommon to see them growing in full sun.
    Altitude Chusquea spp. are typically abundant in zones up to 1500 m, above which their growth was noted to be stunted, not reaching more than 2–2.5 m in height. Above 2000 m, they typically do not reach more than 1 m in height.
    Water Chusquea spp. grow near water, and their root systems are often partially inundated in stream beds.
    Temperature Chusquea spp. grow in cooler microclimates.
    Grade Chusquea spp. grow across all grades, including very steep hillsides. They are considered to prevent erosion.
    Soil type Chusquea spp. can grow in a variety of soils. They will often compact soil and create high duff levels with their own leaf foliage, which is thought to play a role in adding nutrients to the soil.
    Species interactions Chusquea spp. are most commonly associated with another commonly foraged species: Ramaria flava (Changle) and other plant varieties, including Aristotelia chilensis (Maqui), Luma apiculata (Arrayan), and Araucaria araucana (Pewen). They are also commonly associated with several small mammal and bird species.
    Table 5
    Table 5. Biocultural keystone attributes of <em>Chusquea</em> spp. in the southern Andes.

    Table 5. Biocultural keystone attributes of Chusquea spp. in the southern Andes.

    Attribute Indications of biocultural keystone species
    Intensity, type, and multiplicity of use 62 identified historical and current uses related to construction, food production, medicine, artisanry, and spirituality.
    Naming and terminology in a language Several diverse naming schemes are used to refer to the species. Widespread use of Indigenous nomenclature in Mapudungun persists.
    Chusquea quila is referred to as kila or kilautre.
    Chusquea culeou is referred to as koliwe, colihue/coligue, coles, or rëngi.
    Caña de kila/koliwe is used to refer to bamboo stands.
    Kilatral or koligual refers to a forested sector dominated by bamboo.
    Role in narratives, ceremonies, or symbolism (i) Chusquea spp. are symbolized as messengers, protectors, and companions.
    (ii) The vertical stature of Chusquea spp. represents a connection between wenu mapu (the land above the “heavens”) and wallmapu (the land and name of the Mapuche territory).
    (iii) Bamboo stocks have numerous uses in ceremonies and traditional healing practices.
    Persistence and memory of use in relationship to cultural change (i) Chusquea spp. are still used frequently and in diverse forms.
    (ii) Traditional Ecological Knowledge of Chusquea spp. use and harvesting remains widespread among rural and Indigenous communities.
    (iii) Myths of bamboo flowering seem to have been adopted by the greater Chilean culture.
    Level of unique position in culture While wood has been noted to be substituted for some of the construction-related uses of Chusquea species, no native species were found to replace the Chusquea species’ breath of applications or their cultural role.
    Extent to which they provide opportunities for resource acquisition from beyond the territory Chusquea spp. are exchanged as raw materials for construction purposes and in the form of finished products (conserves, artisanal goods, etc.).
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    Home > VOLUME 30 > ISSUE 3 > Article 26 Research

    From “power over” to “power with”: resilience of the tomato value chain in the Upper East Region of Ghana

    Jeangros, L., J. Jacobi, J. Six, and K. Benabderrazik. 2025. From “power over” to “power with”: resilience of the tomato value chain in the Upper East Region of Ghana. Ecology and Society 30(3):26. https://doi.org/10.5751/ES-16217-300326
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    • Laurence JeangrosORCID, Laurence Jeangros
      Department of Strategy, Globalization and Society, University of Lausanne (HEC Lausanne), Switzerland; Enterprise for Society Center (E4S), Ecublens, Switzerland
    • Johanna JacobiORCID, Johanna Jacobi
      Institute of Agricultural Sciences, ETH Zurich, Switzerland
    • Johan SixORCID, Johan Six
      Sustainable Agroecosystems Group, Institute of Agricultural Sciences, Department of Environmental Systems Science, ETH Zurich, Switzerland
    • Kenza BenabderrazikORCIDcontact authorKenza Benabderrazik
      Sustainable Agroecosystems Group, Institute of Agricultural Sciences, Department of Environmental Systems Science, ETH Zurich, Switzerland

    The following is the established format for referencing this article:

    Jeangros, L., J. Jacobi, J. Six, and K. Benabderrazik. 2025. From “power over” to “power with”: resilience of the tomato value chain in the Upper East Region of Ghana. Ecology and Society 30(3):26.

    https://doi.org/10.5751/ES-16217-300326

  • Abstract
  • Introduction
  • Theoretical Background
  • Methods
  • Results and Discussion
  • Conclusion
  • Responses to this Article
  • Acknowledgments
  • Data Availability
  • Literature Cited
  • climate resilience; food system; Ghana; power relations; tomato value-chain
    From “power over” to “power with”: resilience of the tomato value chain in the Upper East Region of Ghana
    Copyright © by the author(s). Published here under license by The Resilience Alliance. This article is under a Creative Commons Attribution 4.0 International License. You may share and adapt the work provided the original author and source are credited, you indicate whether any changes were made, and you include a link to the license. ES-2025-16217.pdf
    Research

    ABSTRACT

    Food systems are increasingly subject to shocks (e.g., climate change, pandemics, financial or political crises), threatening food supply both locally and globally. Transforming food systems is urgent to achieve socially just food for all within planetary boundaries. Here, we integrate the analysis of power relations into the concept of resilience by studying the tomato value chain in northern Ghana, which is characterized by both climate shocks and unequal power relations. We address two questions drawing on critical resilience studies: (1) What are the characteristics of power relations between actors in the tomato value chain? (2) How do extreme weather events (shocks) influence power asymmetries between actors in the tomato value chain? Based on our findings, we argue that resilience studies should increasingly integrate a power lens, understanding resilience as a collective goal of food system actors. Our results shed light on the inherent link between power relations and resilience, especially through positive power such as “power with” used to mitigate the effects of a crisis. We observed asymmetric power dynamics in the Ghanaian tomato value chain, with widespread dependencies on credit and loans for farmers, who are then compelled to sell their produce at low prices. Our findings add nuance to the common discourse of female traders being the only power holders in the system.

    INTRODUCTION

    As climate change and environmental degradation lead to increasing weather events and sanitary shocks, food systems are moving further away from their multiple goals of providing food and healthy diets for all, decent livelihoods, and protection to ecosystems, among other things (Campbell et al. 2017). Against this backdrop, the resilience of food systems is key to secure the supply of food in times of crisis (Tendall et al. 2015, Nguyen 2018, von Braun et al. 2021). However, resilience approaches have been criticized for neglecting the social in social-ecological systems (SESs) such as food systems, lacking essential questions about who the winners and losers in different SESs are and why (Côte and Nightingale 2011, Dixon and Stringer 2015). By focusing on these systems’ adaptive capacity, this oversight has indirectly favored the status quo of unequal and unsustainable systems configurations instead of transforming them (Côte and Nightingale 2011, Walker and Cooper 2011, Beymer-Farris et al. 2012, Brown 2014). Moreover, power in food systems has been studied mainly from a structural perspective, focusing on how food production systems are intrinsically linked to specific economic orders at different historical moments, so-called food regimes (Friedmann, 2005, 2016, McMichael 2009), or globally by looking at the influence of corporations on the global food system (Clapp and Fuchs 2009). However, the examination of contemporary power relations at different scales, including the relational one, remains incomplete in food systems, even though these dynamics significantly influence resource allocation and access (Jacobi and Llanque 2018, Jacobi et al. 2021).

    In Ghana, tomatoes account for 35% of households’ vegetable expenditure, and they are part of nearly all household meals (Van Asselt et al. 2018). Tomatoes are consumed either fresh or in the form of tomato paste. It is estimated that approximately 90,000 farmers are involved in tomato production, and > 300,000 people are linked to the tomato sector nationwide (https://www.wathi.org/debat_id/developpement-de-lagriculture/wathinote-developpement-de-lagriculture/ghanas-tomato-processing-industry-an-attractive-investment-option-in-2016/). Ghana’s imports of tomato paste began to soar in the 1990s (Baba et al. 2013, Britwum 2013, Snels et al. 2018, Frimpong Boamah and Sumberg 2019). The country’s growing dependence on imported paste and the inability of domestic factories to compete have made this case a prominent example of “import surges,” highlighting the inequities of international trade agreements (Frimpong Boamah and Sumberg 2019).

    The tomato value chain is understood here as the production, supply chain, and consumption of fresh tomatoes from different parts of Ghana—mainly the Brong-Ahafo and the Upper East regions—and from other adjacent countries. This value chain is influenced by external factors such as tomato paste imports and agricultural and trade-related policies. This tomato value chain has been described as highly unequal because producers have little agency and sellers have restricted access to the market (Robinson and Kolavalli 2010a, van Wesenbeeck et al. 2014, Kolavalli 2019). The supply chain is organized by women traders from the South, known as “market queens,” who are the main intermediaries in the chain and are organized in strong market associations. It has been observed that women-led market associations emerge as culturally acceptable responses to women’s restricted access to land, education, and formal employment, enabling income generation through care-related activities with other women (Scheiterle and Birner 2018). Some authors, however, point to these market queens as exploiting farmers through underpayment (Ngeleza and Robinson 2013, van Wesenbeeck et al. 2014, Amikuzuno et al. 2015, Kolavalli 2019). This market structure, characterized by concentrated and organized intermediaries, has significantly impacted tomato farmers in the Upper East Region (UER), particularly in their efforts to secure supplies for the national market during the dry season from December to April (Quaye 2006, Abdulai et al. 2018, Ghana Statistical Service 2018). Market queens have increasingly sourced fresh tomatoes from Burkina Faso instead of the UER (Awo 2010). During the rainy season, from April to December, the country’s demand is predominantly met by the Brong-Ahafo region in the south, which produces rain-fed tomatoes. Here, we focus on the tomato value chain from the UER.

    The UER remains one of the areas in the country most vulnerable to climate change due to its geographical zone and the uneven territorial development that has disadvantaged the northern regions to the benefit of export-oriented industries and crops located in the south (Tambo 2016, Abdulai et al. 2018). Approximately 56% of the land area is classified as arable, with some districts reporting that > 90% of the population is engaged in peasant farming, making agriculture a primary livelihood activity (MOFA 2022, Baffoe et al. 2021). Land tenure ranges from inherited to rental arrangements. However, factors such as deagrarianization, urbanization, migration, land reform, resettlement, and re-peasantization have significantly altered traditional land systems, with ownership increasingly contested (Akolgo-Azupogo et al. 2021). Traditional agroecological knowledge remains the dominant adaptation strategy, supporting diverse cropping systems that range from subsistence staples such as rice, maize, groundnut, and sorghum to fruits and vegetables such as tomato, onion, and pepper (MOFA 2022, Baffoe et al. 2021). The region has received particular attention in the scientific literature over the last decades because it is known to have the highest prevalence of poverty and food insecurity in the country (Abdulai et al. 2018, Adu et al. 2018, Fagariba et al. 2018). In this context, the need to enhance the climate resilience of smallholder farmers has been identified as a priority, especially in vulnerable communities such as in the UER (Tendall et al. 2015, Tambo 2016). Benabderrazik et al. (2022) emphasize the importance of addressing the broader social and power dynamics in their analysis of the resilience of smallholders in the UER, going beyond climate change shocks and adaptations.

    Here, we aim to address the dual objectives of understanding how to increase resilience and incorporate power analysis in food systems research. By exploring these themes, we aim to foster reflection on the potential for transformation in food systems, emphasizing the importance of moving beyond adaptation in certain contexts. We understand transformation as fundamental shifts that significantly change the interactions and feedback loops between humans and the environment, whereas adaptation refers to adjustments that preserve the system’s core functioning without restructuring its underlying processes (Olsson et al. 2015). Additionally, we aim to fill an empirical gap concerning the reaction of the system’s actors to climate shocks and stresses, focusing on whether and how power relations are modified during such events.

    Against this background, we address the following research questions.

    1. What power relations characteristics influence the climate resilience among actors of a value chain?
    2. How do shocks such as extreme climatic events influence power asymmetries among actors of a value chain?

    To characterize power relations among actors, we build upon Gaventa’s (2005) power cube framework. We integrate the dynamic nature of resilience into this framework by incorporating elements of resilience theory, with the aim of contributing to the nascent literature on power relations and critical resilience in food systems (Hendrickson 2015, Rotz and Fraser 2015, Walsh-Dilley et al. 2016, Boillat and Bottazzi 2020, Haller et al. 2020).

    We first present the theoretical framework that integrates power into resilience approaches, followed by the methodological approach and the case study context. We structure the results around the four identified spaces of power in the tomato value chain, followed by an analysis of how these spaces are affected by climate shocks. We conclude by discussing the implications for resilience and the transformation of food systems.

    THEORETICAL BACKGROUND

    Resilience in social-ecological systems research

    The plethora of existing resilience research mostly focuses on the capacity to withstand and to recover from shocks, without addressing the space where decision-making takes place during these critical periods (Kull and Rangan 2016). This oversight has led to resilience studies frequently failing to address the fundamental questions of what resilience is and whom it benefits (Côte and Nightingale 2011), thereby overlooking essential issues of agency and power within SESs (Ifejika Speranza et al. 2014, Mukhovi et al. 2020). Here, agency is understood as the capacity of actors to act and change their environment (VeneKlasen and Miller 2002, Gaventa 2005) and power “in relation to how spaces for engagement are created,” to envision transformative possibilities of citizen action on their environment (Gaventa 2005:6). The application of resilience in research studies and development practices has thus overlooked important causes of vulnerability, which may have led to the promotion of top-down solutions that fail their purpose (Davidson 2010, Walsh-Dilley et al. 2016). In this regard, the current literature has failed to offer a framework that takes power dynamics into account in SES resilience (Côte and Nightingale 2011, Stagner and Mulundano 2024). From this perspective, we integrate power as a critical element to address the resilience of food system stakeholders. For this purpose, we use Gaventa’s (2003, 2005) power cube framework to analyze power and integrate social and power dynamics as important determinants of resilience (Köpke 2021, Benabderrazik et al. 2022, Stagner and Mulundano 2024). The power cube offers a framework for analyzing spaces and forms of power that are found in the value chain, including consideration for spaces of empowerment and transformation. The latter consideration helps us to understand how resilience can be built from an individual and collective power perspective.

    Power in the resilience literature: from adaptation toward transformation?

    Resilience is defined as the magnitude of disturbance that can be tolerated before an SES moves to a different region of state space controlled by a different set of processes (Carpenter et al. 2001). In other words, it has often been described as the ability of a system to adapt and remain in a desirable state (https://www.resalliance.org/adaptive-cycle) and thus reduce uncertainty (Scoones and Stirling 2020). However, the reality shows a rather wide range of actors with diverse perspectives and interests concerning the supposed desirable state of the SES in play, resulting in unequal outcomes and trade-offs (Côte and Nightingale 2011, Beymer-Farris et al. 2012, Fabinyi et al. 2014). Scoones and Stirling (2020) underline how approaches to sustainability and development often rely on expert-defined solutions, which obscures the very notion of uncertainty, thereby concealing possible futures and whose interests are pursued. Côte and Nightingale (2011:485) argue that it is only by drawing our attention to “issues of power, authority and complex rationalities” that we are able “to ask difficult questions about whose environments and livelihoods we seek to protect and why.” In particular, normative questions such as “resilience of what, to what, for what purpose, and for whom?” help bring a critical understanding of what a desirable state means for the different actors of the system (Lebel et al. 2006, Beymer-Farris et al. 2012, Ingram et al. 2023). Furthermore, the focus on adaptation in resilience studies made critical scholars assess the actual stance of resilience as maintaining the status quo of potential unsustainable systems rather than creating opportunities for transformation (Birkenholtz 2011, Walker and Cooper 2011, Watts 2011, Beymer-Farris et al. 2012, Turner 2013, Brown 2014). They add that this seemingly neutral position is the reason why the concept of resilience has recently often been brought to political arenas and decision-making (Turner 2013, Redman 2014, Kull and Rangan 2016). Birkenholtz (2011:299) summarizes some of these critiques by stating that resilience has “(...) a rationalist view of institutions (...) that leads to a focus on social capital and its derivative ‘adaptive capacity building’, which can be indexed and then addressed in technical and managerial terms (...) rather than leading to the questioning of the structure of resource allocation or issues of social justice, human security, and equity.”

    Thus, resilience is seen by various authors as a technocratic and top-down understanding of SESs because of its approach considering SESs as manageable and predictable (Birkenholtz 2011, Côte and Nightingale 2011, Beymer-Farris et al. 2012, Brown 2012, Turner 2013), and as “artificially apolitical” because of its lack of consideration of the different interests present in SESs and the politics in which they are embedded (Zurek et al. 2022, Ingram et al. 2023). This critique echoes long-standing concerns in development studies about the framing of deeply political processes into technical ones: Although resilience has been portrayed as a “will to design” (Grove 2018), Côte (2019) argues that it is better understood as a “will to adapt.” This “will to adapt” is then closer to Li’s (2007) critical understanding of development as a “will to improve,” both of which are fundamentally political in nature. However, a more nuanced perspective highlights that resilience can be emancipatory and transformative when politicized. Grove and Chandler (2017) show how feminist and decolonial approaches can help politicize resilience by understanding it as relational and situated, thus overcoming its top-down technical attributes.

    The power cube framework

    Power has been conceptualized and explained in many different forms by many different authors. For example, Foucault (1982) considers power to be pervasive, diffusing itself through discourse and shaping or “producing” regimes of truth and knowledge and thus being productive. It has been criticized for leaving little space for individuals’ agency (Ahlborg and Nightingale 2018). By contrast, Bourdieu (1989) considers that power is embedded in social structures and everyday practices (habitus), reproducing and legitimizing social hierarchies through symbolic means. Individuals do have some agency to adapt or subvert, but they are bounded by societal structure. Lukes’ (2004) understanding of power offers a combination of views through a three-dimensional understanding of power, distinguishing a visible “first” dimension related to who can shape concrete decisions, a “second” dimension related to who sets political agendas, and a more subtle “third” dimension wherein power shapes people’s perceptions and preferences (close to Bourdieu’s understanding of symbolic power and Foucault’s productivity of power). His understanding of power therefore allows us to understand social life as an interplay between both structural determinism and individual agency (Lukes 2004).

    Overall power is an “essentially contested concept” (Gallie 1955), with scholars continuously debating its definition, scope, and appropriate application across disciplines. The goal is therefore to mobilize a definition of power that is best suited to the study’s analytical purpose. Here we use the power cube, a tool developed by Gaventa (2005) that has been used to characterize power in food systems (Nelson et al. 2014, Jacobi and Llanque 2018). Gaventa (2005) builds upon Lukes’ (2004) three dimensions of power, understanding power as relational (created between individuals), contingent (specific to the context and relation), and, to some extent, productive (creating knowledge and discourses, along Foucault’s line). The focus of the power cube is to understand how different actors influence decision-making in different spaces, i.e., arenas, which can be either physical or virtual, where interactions, negotiation, and decision-making take place (Gaventa 2003). This focus formulates a response to a general concern, also in food systems (Jacobi and Llanque 2018), about whether participation and inclusion mechanisms create real shifts of power toward more democratic spaces or, on the contrary, maintain unequal status quos (Jacobi et al. 2021). Levels of power (from local to global), as well as different forms of power (along Lukes’ three dimensions of power), are addressed (Gaventa 2005). Spaces, levels, and forms of power represent the three dimensions of the power cube developed by Gaventa (2005; Fig. 1, Table 1).

    The power cube is thus more than a descriptive framework because it can help to identify possible pathways for citizen empowerment by the creation of new democratic spaces (Gaventa 2005). However, these actions are also achieved using other forms of power, described by some scholars (VeneKlasen and Miller 2002, Pantazidou 2012) as positive power, i.e., the “capacity and agency to be wielded for positive action” (Gaventa 2005:9), or “power to,” “power with,” and “power within” (VeneKlasen and Miller 2002).

    Overall, Gaventa’s (2005) approach to power acknowledges individuals’ agency and understands power as a resource that is unequally distributed (Ahlborg and Nightingale 2018). Here, we use the power cube in a first step to analyze the power relations within the tomato value chain of Ghana. We then use the positive power typology in a second step to analyze whether spaces are created or claimed through “power with” (the capacity to work collectively towards a certain goal), “power within” (the individual’s awareness about their agency to bring positive change in society), or “power to” (the individual’s capacity to influence their own life). The rationale taken here is that to reach a more sustainable and equal food system, all actors involved in it should be able to participate in its governance and define its norms and rules (Walsh-Dilley et al. 2016).

    METHODS

    Geographical scope and historical context: the tomato system in the Upper East Region of Ghana

    The UER is a savanna zone in the northeast of Ghana, bordered by both Togo and Burkina Faso (Armah et al. 2011). The region is characterized by a unimodal rainfall pattern starting in May and ending in September. Most of the households (76.4%) are located in rural areas (Antwi-Agyei 2012), and agriculture, mostly rain-fed, is their predominant economic activity (Kumasi et al. 2019). During the rainy season, farmers produce staple grains such as maize, millet, sorghum, and rice, mostly for their own consumption and to sell on the local market (Antwi-Agyei et al. 2012, Fagariba et al. 2018). In the dry season, farmers with access to irrigation (estimated ~50%) grow high-value vegetables such as tomatoes, onions, and peppers for the local and national markets, representing their main source of cash income (MOFA 2011, Fagariba et al. 2018).

    The UER has historically been sidelined in national development policies because of the high-value economic activities in the South such as cocoa production, timber harvesting, and gold mining, which have attracted political attention and have used, since colonial times, cheap labor mainly coming from the North (Konadu-Agyemang 2000, Abdulai et al. 2018). However, the region managed to thrive economically from the 1960s until the mid-2000s, mainly due to tomato production. It supplied dry-season (December to April) tomatoes for both national demand and a tomato paste factory located in the UER (Awo 2010, Robinson and Kolavalli 2010b, Britwum 2013). The Pwalugu Tomato Factory in the UER was established in 1967 by the first Ghanaian government and its Prime Minister Dr. Kwame Nkrumah, an iconic figure who fought for the country’s independence through import substitution, among other policies (Frimpong Boamah and Sumberg 2019). The factory closed in the late 1980s due to structural reforms and operational challenges. In recent years, it has seen multiple failed attempts at reopening, including refurbishments and collaborations with private firms (Robinson and Kolavalli 2010b).

    In addition, in the mid-2000s, market queens increasingly began sourcing their tomatoes from Burkina Faso. The main reasons behind this shift are not clear but might be a combination of crop failure in UER (due to pests and diseases); the good quality of Burkinabe tomatoes, reducing transport losses; the high quantity of tomatoes produced in Burkina Faso, ensuring availability; and the possible interest of crossing the border allowing for trade in both directions (Awo 2010, Robinson and Kolavalli 2010a,c).

    This market loss led to an economic decline in the UER, where farmers now cultivate less profitable crops such as peppers or onions (Awo 2010). The region is further characterized by high levels of poverty and food insecurity, with often up to six months of food shortages annually (MOFA 2010, Ghana Statistical Service 2018). It is also considered one of the most vulnerable regions of the country to climate change (Wossen and Berger 2015, Tambo 2016). Drought and flood events, referred to here as “climate shocks,” are forecasted to increase in both frequency and intensity (UNEP and UNDP 2012, Samaddar et al. 2015). In addition to climate shocks, farmers are exposed to market disturbance and shocks such as price volatility (Benabderrazik et al. 2022). Farmers’ strategies to mitigate these stressors usually encompass changing the timing of planting and diversifying their crops (Laube et al. 2012, Antwi-Agyei et al. 2015, Tambo 2016, Kumasi et al. 2019).

    Data collection

    We took a qualitative research approach because power relations form social structures, which are best approached through qualitative means (Winchester and Rofe 2016). Data collection took place in five locations (Fig. 2) with the help of two research assistants from October to December 2019. It was complemented by a literature review, including local newspaper articles.

    We conducted 34 semi-structured interviews in the UER using a purposeful, stratified sampling strategy (Patton 2015). The goal was to ensure representation from each type of actor in the system to capture diverse perspectives. Initially, we conducted at least one interview with each actor type. Following this, a snowball sampling technique was employed, targeting a minimum of two individuals per actor group to explore the diversity of experiences. When interviews within the same actor group revealed a wide range of responses, additional interviews were planned to understand better the sources of this diversity and the commonalities in their experiences (Table 2). These interviews were supplemented by four expert interviews and one focus group comprising one representative from each actor category involved in the tomato value chain in the UER. The interviews were transcribed in English together with the research assistant present at the interview, speaking both English and the language spoken by the interviewee.

    Data gathered through the literature review was instrumental in contextualizing the interviews. In particular, it helped to identify how certain narratives reflected broader discourses present in the community. Local newspapers, for example, offered valuable insight into, for example, the role of the tomato processing factory in local political rhetoric during election periods. More broadly, the triangulation of diverse sources proved essential for analyzing power dynamics because power is not only enacted through structures and relations but also articulated through discourses.

    Data processing

    The transcriptions of interviews and the focus group were analyzed using Atlas.ti 8.4.4 software (ATLAS.ti Scientific Software Development, Berlin, Germany) through qualitative content analysis, following Bengtsson’s (2016) four steps to minimize researcher bias and draw realistic conclusions. First, data decontextualization was achieved by screening all transcriptions and coding in the smallest meaning units possible. The codes were chosen both deductively, based on the questions raised in the interview guides and the research questions, and inductively, by identifying emergent themes across interviews (see Appendix 1 for the codes created). Second, recontextualization was performed by revisiting the transcriptions with the finalized codes to ensure that no relevant data were overlooked, especially in uncoded sections, and by verifying their alignment with the research questions. Third, categorization was carried out by assembling codes around domains that were taken from the theoretical framework (e.g., spaces of power or strategies put in place to react to shocks; see Appendix 1 for the groups created). Fourth, the compilation balanced both manifest (surface-level, explicit interpretations of informants’ words) and latent (in-depth exploration of underlying meanings) approaches. This dual-layered analysis sought to capture both explicit statements and nuanced, implicit patterns, which are key in power relations analyses. The iterative coding process and emerging categories were continuously discussed and validated within the research team to ensure consistency and accuracy in interpretation.

    RESULTS AND DISCUSSION

    Spaces and forms of power

    We found four spaces of power in the UER tomato value chain (Fig. 3): production, selling, processing, and consumption. The production space is influenced by the production of tomatoes in Burkina Faso, which has decreased market access for UER farmers to major cities in the southern part of Ghana. According to our data, no UER tomatoes were sent to supply the southern part of Ghana, confirming the loss of market opportunities for UER farmers. However, farmers still cultivate tomatoes to a smaller extent and sell them on the local market. Additionally, a defunct processing plant was identified as still influencing the tomato value chain through political discourses and speculative promises. Lastly, the Ghanaian consumption encompasses both consumers in the UER and in the southern Ghanian marketplaces to acknowledge the historical link between both geographical regions through tomato production and consumption.

    Space 1: production in the UER

    The production space mainly comprises the elements necessary to grow tomatoes: access to land, seeds, inputs, water, and knowledge. Farmers need to invest to produce tomatoes, with the highest costs for inputs being seeds and irrigation (Robinson and Kolavalli 2010b). Most farmers purchase tomato seeds, mostly of local varieties and some of improved varieties, with a small proportion of farmers recycling seeds (Robinson and Kolavalli 2010b). It has been shown that tomato production in Ghana, including small-scale production, was relying heavily on pesticides to avoid losses and meet demands for blemish-free tomato fruits. It has been found that tomato farmers in Ghana use various pesticides, including several unregistered products such as DDT or heptachlor accessed through local input retailers, which pose health and environmental hazards (Bandanaa et al. 2016, Mbatchou et al. 2024).

    Our results indicate that this space is mainly influenced by official governance systems, most importantly, the government and traditional authorities such as traditional village chiefs (Table 3). An element that emerged frequently in the interviews was the distribution of inputs linked to political interests. One farmer described the distribution of inputs from the flagship policy “Planting for Food and Jobs” launched by the political party in power at the time:

    The government helps us. It is us that are not ready to support ourselves. For example, the water we have—we have six bottles—I’ll remove three and ask my friend [member of the same political party] to also take three to them. My friend too will also remove one and give the rest to them [members of the same political party] and their leader too will also take one. So, at the end of the day, only one is available [for everyone] instead of six. (Farmer in the UER, Navrongo).

    Four other farmers and one input supplier mentioned that subsidized inputs such as fertilizers and pesticides are often distributed by the local ruling political party to its members, leaving politically unaffiliated farmers with the leftovers.

    You know they are their own power, so when they give to the party executive, you know when the MP [Member of Parliament] comes, he gives something [referring to farm inputs] to the party executives. So they share among themselves. So when you have a relative who is executive, then he can offer you something. (Farmer in the UER, Navrongo).

    From a land-tenure perspective, few claimed spaces were found. For instance, women, who traditionally cannot own land in the UER (Antwi-Agyei et al. 2018), accessed land with the help of a nongovernmental organization (NGO) and by negotiating with the chiefs. However, situations of “tutorat,” a patronage relationship providing land-use rights to landless farmers or migrants (see Colin 2013), were widespread, leading to forms of non-monetary payment for access to land, leaving producers with informal and insecure land access.

    I begged for the land from people to farm. And after harvesting, I can give them some of the food and the following year, they will allow me to farm (...). (Female farmer in the UER).

    During peak agricultural periods such as harvesting or weeding, farm labor was frequently carried out by young individuals, including school-aged children. This result points to a structural reliance on low-cost labor within the agricultural sector, which eventually limits education and opportunities for rural youth.

    All farmers were members of various farmers’ groups that functioned as social support systems. Some of these groups operated as “tontines,” a collective saving system prevalent in West Africa, where members contribute a set amount of money regularly. This system enables members to access the collective savings during times of crisis or need, with the expectation of repaying the group when able. Other groups were established to facilitate the receipt of support such as grants or inputs from NGOs.

    Finally, a previous study shows that farmers do not have access to sufficient external inputs, which underlines the importance of this issue for their work (Benabderrazik et al. 2022). This insufficiency makes farmers largely unable to shape and shift their position in the system, shedding light on an important system lock-in. Apart from a women’s group, farmers in our sample depended largely on government subsidy schemes and on loans provided by input suppliers to access inputs. Even though Ghanaian farmers were often part of a farmers’ association, these associations were not used to empower them in their commercial activities, such as by setting a common price or establishing contracts with buyers. Awo (2010) already observed how this poor level of organization among farmers puts them in unfavorable positions in their commercial relations.

    Altogether, this space of production displays “hidden” power of political agendas at regional and national levels and is rather “closed,” with few possibilities for women to access land, for example. Solidarity systems in the form of tontine create “claimed” spaces through “power with” for farmers to access necessary external inputs for their production.

    Space 2: selling in the UER

    Marketplaces are the spaces of exchange among various actors, operating as an arena where farmers, market queens, middlemen, and consumers meet (Table 3). They shed light on the multidimensional dynamics unfolding within this single space.

    The selling space was “claimed” and “visible” at the local level: the women’s sellers, organizing the market in the UER, did not control or restrict access to the selling space. Anyone (farmers, sellers, etc.) wanting to sell products on the market could do so, which is in stark contrast to how southern marketplaces are managed. The selling spaces were mostly organized as “tontines,” similar to farmers in the production space (see Space 1). Higher authorities had limited influence on the market. It was reported that the district assembly collected tax on the marketplace, but this would not significantly influence the work of the sellers on the market.

    Although the marketplace is described as a claimed, visible space, it is contrasted with the southern marketplace, where some tomatoes historically bought from the UER are now sourced from Burkina Faso (see Fig. 3, grey box). Interviews revealed the significant risks faced by market queens, leaders, and loaders in fetching tomatoes from Burkina Faso, including frequent truck accidents, poor road conditions, and armed robbery. Market queens also reported lending money to farmers for inputs, assuming the financial risk if the crops failed. Interviews revealed that the market queens’ association was also working as a tontine, and was controlling access to the major marketplaces in Accra or Kumasi to control the prices of various products, including tomatoes.

    Public discourses from both the government and newspapers blame market queens for the exploitative relationships they hold with farmers by providing loans and then requiring farmers to sell their products at a low price (Lyon 2003, Kokutse 2009, Britwum 2013). Newspapers even hold market queens as responsible for tomato farmers suicides in UER, after farmers lost their market to Burkina Faso in the 2010s (Akapule 2009). However, there is also a more nuanced literature that underlines their crucial role in the supply chain and their efficiency in conducting a highly risky activity, both in their practices (e.g., road accidents, rotten tomatoes) and by providing loans to farmers that may experience shocks, without access to formal credit (Lyon 2003, Awo 2010, Scheiterle and Birner 2018). This nuance is echoed by our observations, which demonstrate the high levels of risk that market queens face in their activities due to accidents and robberies on the road, resulting in losses of tomatoes and money. As such, the strong market associations of market queens appear here to be, first and foremost, a necessity to de-risk activities, allowing them to supply the market through mutual empowerment—the so-called “power with.” Here, it seems that this “power with” is partly built upon the ability to exclude members from their association.

    We are under the Queen and we have authority from Asantehene [king]. So, if you are not part of our group, you can’t come with your load to sell. There are rules that govern us. (Market queen, Kumasi).

    This structure thus empowers the limited group of individuals who form the market queens, a role primarily inherited from their mothers (as indicated in interviews). This finding raises questions about the extent to which “power with,” based on exclusion, can genuinely be considered mutual empowerment and found in “closed” spaces.

    At the same time, government interventions aimed at “formalizing” the sector were on the rise, and marketplaces in Kumasi and Accra were targeted. However, interviews revealed that these initiatives often seemed to have hidden agendas, frequently acting as covert real estate projects disguised as efforts to improve the conditions of market workers. In this regard, such dynamics were articulated by a representative from an informal workers’ union.

    They [Accra Metropolitan Assembly] built a new market, and then those who were occupying the base earlier, they promised them that after the building, they were going to reallocate a place for them, but unfortunately, since the authorities, even before building, they have already allocated their own people. And then, even those who end up getting some of the space, the amount [taxed] is too high. (Union representative of informal workers, Accra).

    The space was thus undergoing a potential transformation, with a top-down desire to formalize the sector, showcasing the enactment of hidden power.

    Space 3: processing space

    We identified a processing space, referring to a defunct factory, that was still present in the collective imagination. Many people viewed it as a failure of the government to support the region. Politicians regularly used the promise of revamping the factory during elections to gain votes.

    Revamp it? Ha, that was last year’s issue, I don’t know politicians, all you know [is] when they do it, that it is, I don’t think [they will revamp the factory], they keep on talking about it. (Extension officer, Navrongo).

    An extension officer specified that even if the factory were to resume operations, it would not become competitive, even at maximum production, due to imports of low-priced tomato paste. Ghana’s trade policies, characterized by the country’s membership in the World Trade Organization, the Economic Community of West African States, and the Economic Partnership Agreement signed with Europe, set a low tariff on imported tomato paste in the region. Currently, all tomato paste consumed in Ghana is imported, mainly from China (FAOSTAT 2024).

    Thus, this space is shaped by international trade agreements and used by political actors at national and regional levels to gain votes, thereby displaying hidden power. The space is predominantly closed, as the primary beneficiaries, namely tomato farmers, have limited means to influence it. In the past, farmers attempted to create a claimed space by blocking roads to prevent trucks from going to Burkina Faso to buy tomatoes. However, the police intervened, enforcing the trade agreements with Burkina Faso (Awo 2010). These trade agreements represent visible power.

    Space 4: Ghanaian consumers

    Consumers in the UER have limited influence on supply due to their relatively small market size compared to the larger markets in the southern part of the country, such as Kumasi and Accra. All vegetables are purchased at the local marketplace, where we observed varying prices from different sellers, primarily due to differences in tomato quality.

    The southern cities of Accra and Kumasi, the two largest cities in Ghana, were witnessing changing consumption patterns of both fresh and processed tomatoes. A rising middle class is increasingly aware and interested in the nutritional content and the effects of pesticide use on the health and safety of fresh and transformed tomatoes. Tomato paste imported from China has been assessed as having a lower quality because of a lower concentration of nutrients, as well as additives such as fiber, starch, dextrose, and colorants that are not advertised on the label (Malet 2017; interviews). This can be viewed as a claimed space where access to knowledge and decent livelihoods transform the goals of the tomato value chain, shifting the focus from merely taste and calorie intake to nutritional value. Some interviewees saw this trend as an opportunity to relocate tomato production and processing in Ghana during the dry season, with shorter supply chains allowing for more transparency. However, a technical difficulty arises because tomatoes for processing and fresh tomatoes do not have the same properties. Processing tomatoes need to have high liquid content and soft skin, whereas tomatoes for fresh use need strong skin and a lower liquid content so that they can be transported.

    Overall, spaces of consumption are ambivalent. From a consumer’s perspective, it has been shown that consumers are increasingly eating tomatoes, be it processed or fresh (MOFA and IFPRI 2020). The agency of consumers is thus mainly expressed through the increase in tomato consumption. The choice of origin and production practices has been driven by other structures at the global level, such as trade agreements, and at the national level, with the type of agriculture pushed by the government. In this regard, we understand this space of decision as closed and invisible in the eye of the consumers. Although the interviews revealed some space claimed by consumers for increased information on safety and nutritional content, it remains marginal.

    Effects of climate shocks on spaces and forms of power

    With the increasing frequency of climate shocks such as droughts and heavy rainfall, it is crucial to reassess how spaces and forms of power operate in response to these events. Although the above analysis provides an overview of power dynamics in the tomato sector, it mainly offers historical and current perspectives. The projected increase in extreme weather events in Ghana leads us to question: How will these spaces and forms of power respond to a climate shock in the future? We first analyze how actors respond to shocks, mainly through mutual support, and then discuss the implications for resilience studies.

    Mutual trust and support among market chain actors

    From a value-chain perspective, interviews revealed that all actors were negatively affected by shocks in their activities (Table 1), with varying degrees of intensity (Table 4). Actors with economic activities in both Ghana and Burkina Faso, such as market queens, leaders, loaders, sorters, and drivers, were less vulnerable because they could work in either the UER or Burkina Faso. Conversely, the most affected individuals were those who had no alternative income source to compensate or overcome this lack of income, regardless of the type of actor. In general, farmers were the most reliant on other actors, through credits to overcome the shocks.

    At the individual level, our results show that actors used different strategies to overcome stress and shocks such as diversifying work, selling animals, etc. In addition, all interviewees relied on help from within their social circles, exhibiting strong ties within their communities. The interviews and the focus group revealed two main types of support: one internal to the tomato value chain (e.g., a credit from an input supplier to a farmer) and one external to it (e.g., families, neighbors’ associations, tontine).

    They [farmers] sell their animals, to settle [their debts with me]. If they didn’t settle, it means my business would collapse. (Example of internal support; male input supplier in UER, Navrongo).
    We the farmers have that group to always sit together to talk together and also make little contribution [money](...). If there’s anyone in need, we can use that money to help the person and the person will pay back later so that we can continue our work. (Example of external support; female farmer in UER, Navrongo).

    In general, actors were rather seeking help from their peers than from other actors, showing that levels of trust are higher within the same groups of actors than between two different actor groups. Similarly, trust relations between two members of the same geographical community, for example, local input suppliers and farmers, were stronger (farmers were stated to always pay back) than between farmers and traders (the latter complaining about not being paid back). A trader from the south explained that she was financing farmers through credits and loans in nearby regions of Ghana, but not in Burkina Faso, because they were not trustworthy.

    I give them [Ghanaian farmers from Southern regions] money to do the work. When it’s ready, they bring it to me to sell. (....) [In] Burkina is not the same (...) they don’t get good harvest and we run at a loss. And you would have to give them new money to cultivate again and when they get profits, you would pay for the loss. (Market queen from Kumasi).

    Mutual support was thus widespread within both geographically and activity-based connected communities, demonstrating “power with” mainly at the local level.

    Climate shocks and actors’ resilience building

    Our results show that climate shocks triggered a certain level of resilience in the actor configuration. However, they did not unleash a structural transformation of the power relations in the value chain or of solidarity across the value chain’s actors. Rather, resilience was sought at the individual level within the same group of actors or at the household level. The impacts of droughts or heavy rainfalls affected actors that were in an unfavorable power position, such as farmers or individuals without multiple jobs, more severely than those in favorable power positions, such as loaders being able to be employed within other commodities’ value chains. However, it seemed that no groups of actors managed to take advantage of the situation to change the relations to their advantage. All were suffering losses after extreme climatic events, with varying levels of intensity proportional to their adaptation strategies and resources. In other words, opportunities for transformation were constrained, as the system only permitted adaptation rather than deeper change.

    Taking a systems perspective, shocks were strengthening social ties both locally (e.g., communities) and within actors’ groups (e.g., market queens) that can be characterized as “power with” (Fig. 4). This mutual support was provided mostly among geographically close actors, revealing that they were shared among members of the same community. Distrust between geographically remote actors such as southern traders and farmers were expressed in the interviews by both parties, and they were partly loaded by past events (shift to Burkinabe production) and public discourses (newspapers, etc.).

    Who would you get to help you? They [market queens] will not help you to succeed. I fight myself and say that God should help me. You won’t get anybody to help you. (Female farmer in UER, Gia).

    This finding contributes to the debate about whether the sociocultural context constitutes a barrier to communities’ abilities to adapt and transform (Antwi-Agyei et al. 2015) or not (Laube et al. 2012). Our results indicate that the sociocultural context is key and provides social security to the actors during a shock. However, these social ties can help actors adapt to a shock but not transform the power relations across the tomato value chain. It could also be argued that the dry-season tomato value chain, which is subject to regular climate shocks, “internalized” a certain magnitude of shock in its functioning, experiencing it as a long-term stress by developing adaptive strategies.

    Adopting a more critical perspective, we observe a gap between the level at which resilience is officially theorized and addressed at governmental levels (Appendix 2), and the level at which resilience is implemented at the very local, interpersonal level. Very few interviewees mentioned institutions such as the government or NGOs as pillars for helping to cope after shocks. Structural transformations such as the discussed revamp of the Pwalugu tomato factory are similarly hampered by international trade agreements that allow for imports of artificially cheap tomato paste from China. This situation aligns with Nightingale’s (2015) critique of how resilience policies often misconceive scale, failing to recognize that resilience is pursued through dynamic, networked, and multiscalar realities of local communities.

    Lastly, various actors, including extension officers and farmers in the UER, saw climate shocks as an opportunity to recover tomato production in Ghana. They explained that due to intensifying armed conflicts in Burkina Faso and heavy rains affecting different regions of Burkina Faso, it could be an opportunity for UER farmers to regain the attention of southern traders. The option of having the tomato processing factory revamped was also seen as an opportunity, even though it would require strong support from farmers to relaunch large-scale production of tomatoes in the region to ensure sufficient volumes for the factory and thus its competitiveness vs. international imported tomato paste.

    Conceptually, the focus has shifted toward viewing the resilience of food system value chain actors as a collective goal, rather than an individual pursuit. In this sense, the methodology we used (Gaventa’s [2005] power cube) to distinguish visible, hidden, and invisible power proved useful to establish and understand the status quo of power relations in the tomato system. However, we found some limitations when analyzing the short-, middle-, and long-term changes in the face of shocks. The power cube could be enhanced by defining more forms and spaces of power to capture more nuanced changes. It could further differentiate, for example, “desirable” from “undesirable” spaces of power by better integrating the expression of power by VeneKlasen and Miller (2002). Lastly, more research on the link between “power with” and exclusion or inclusion in food systems would allow us to shed light on whether it is solely a positive expression of power or not.

    CONCLUSION

    Regarding power dynamics in the tomato value chain, we observed significant power imbalances in the dry-season tomato value chain, where relations of loans and credits are widespread, and tomato production in the North symbolizes past support from the government to the region. Discourses often portray market queens as exploitative and holding disproportionate power in the value chain. Our findings add nuance to this discourse by reflecting on the high risks of market queens’ activities (road accidents, robberies, food loss), their relationship with the leaders, and their role (together with leaders and input suppliers) in enabling production through providing loans and credits.

    We also show how actors react to shocks through “power with,” mainly among communities, significantly contributing to their resilience, but without fostering transformation. The magnitude of shocks observed, and the system lock-ins, did not trigger transformative change in the system’s power relations. Shocks and stresses negatively affected all actors, but those already in unfavorable power positions, such as farmers, suffered the most. A discourse emerged considering shocks as an opportunity to return production to Ghana, partly due to increasing political instabilities and other climate shocks in Burkina Faso at the time.

    In conclusion, in the current context in which the need to transform food systems is increasingly recognized, we stress the importance of systematically recognizing and integrating the link between resilience and power in food systems. An approach to the resilience of food systems that takes account of power dynamics sheds light on issues of inequality and scale because stakeholders are affected differently by shocks, and top-down policies aiming at improving resilience lack understanding of how resilience is operationalized by communities. It also allows us to consider resilience as a common objective rather than an individual effort. Strengthening the resilience of the tomato value chain in the UER could therefore mean a concerted and coordinated effort at local, regional, and national levels and across scales to support farmers and share risks, for example, by reestablishing a tomato processing plant.

    RESPONSES TO THIS ARTICLE

    Responses to this article are invited. If accepted for publication, your response will be hyperlinked to the article. To submit a response, follow this link. To read responses already accepted, follow this link.

    ACKNOWLEDGMENTS

    We are deeply grateful to all those who generously contributed their presence, knowledge, and lived experiences, sharing them with benevolence and helping to shape this research. These valuable insights and perspectives have significantly shaped and deepened our understanding and informed the findings of this study. We sincerely thank Turkson Alichimah for support throughout the research process, particularly in translating and facilitating discussions with some of the individuals we met in Navrongo. This work stands as a reflection of the collaborative effort and shared commitment to advancing knowledge and perspectives in this field.

    Use of Artificial Intelligence (AI) and AI-assisted Tools

    ChatGPT was used as a tool to support the editing process, primarily serving as an English grammar checker to help prevent awkward mistakes on our part.

    DATA AVAILABILITY

    The data and code supporting the findings of this study are available upon request from the corresponding author, Dr. Kenza Benabderrazik. These materials are not publicly accessible due to restrictions such as the potential compromise of research participants’ privacy. Ethical approval for this research was granted by ETH Zurich.

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    Corresponding author:
    Kenza Benabderrazik
    kenza.benabderrazik@usys.ethz.ch
    Appendix 1
    Appendix 2
    Fig. 1
    Fig. 1. Visualization of the power cube with the three types of spaces, forms, and levels. Based on Gaventa (2005:12).

    Fig. 1. Visualization of the power cube with the three types of spaces, forms, and levels. Based on Gaventa (2005:12).

    Fig. 1
    Fig. 2
    Fig. 2. Map of Ghana, with circles showing the locations of data collection.

    Fig. 2. Map of Ghana, with circles showing the locations of data collection.

    Fig. 2
    Fig. 3
    Fig. 3. The spaces of power in the Upper East Region (UER) tomato value chain represented in a value chain form.

    Fig. 3. The spaces of power in the Upper East Region (UER) tomato value chain represented in a value chain form.

    Fig. 3
    Fig. 4
    Fig. 4. The spaces of power when subjected to shocks. Arrows show the direction of movement observed in the levels, forms, and spaces of power used by actors to overcome a shock.

    Fig. 4. The spaces of power when subjected to shocks. Arrows show the direction of movement observed in the levels, forms, and spaces of power used by actors to overcome a shock.

    Fig. 4
    Table 1
    Table 1. Description of the three dimensions developed in Gaventa’s (2005) power cube concept.

    Table 1. Description of the three dimensions developed in Gaventa’s (2005) power cube concept.

    Dimension Description
    Spaces of power Define where and how actors can shape and access their food system, i.e., access to resources and market. Gaventa identifies three spaces: Closed (spaces of decision-making closed to participation), invited (spaces opened up, inclusively or exclusively, to enhance participation), claimed or created (spaces claimed or created by less powerful actors).
    Forms of power A typology of power based on Lukes’ (2004) three dimensions of power, explaining the degree of visibility of a conflict or actor’s voice. Three forms of power are found: visible power (openly visible, such as formal rules, authorities), hidden power (hidden agenda of powerful actors, based on the exclusion of certain groups), and invisible power (most subtle form of power, which shapes psychological and ideological boundaries for participation, similar to Foucault’s [1982] discursive power).
    Levels of power The geographical tiers at which social, economic, and political authority are situated, typically encompassing local, regional, and national governance levels, which are often interconnected and can exist on a continuum. As Nightingale (2015) emphasizes, levels refer to fixed positions within hierarchical governance structures (e.g., national, regional, local), whereas scales are socially constructed, relational, and dynamic, emerging from how actors, knowledge, and resources are organized and experienced across space.
    Table 2
    Table 2. Summary of interviews and focus group participation. F = female, M = male.

    Table 2. Summary of interviews and focus group participation. F = female, M = male.

    Type of actor Number of people interviewed Presence at the focus group
    Farmer 4 M, 2 F 1 F, 2 M
    Hired farm laborer 2 M –
    Extension officer 1 M 1 M
    Nongovernmental organization agent 1 M 1 M
    Input supplier: retailer 3 M 1 M
    Input supplier: national level 1 F –
    Market queen from UER 2 F 1 F
    Market queen from the South 3 F –
    Loader 2 M 1 M
    Sorter 1 F 1 F
    Leader 2 M 1 M
    Market seller 4 F 2 F
    Sellers’ union representative 1 F 1 F
    Expert: professor, ministry representative 3 M, 2 F –
    Table 3
    Table 3. Description of different actors in the tomato value chain and the space(s) in which they engage.

    Table 3. Description of different actors in the tomato value chain and the space(s) in which they engage.

    Actor Description Spaces in which they are active
    Upper East Region (UER) farmers Produce and harvest tomatoes, mainly selling at regional markets in UER or to bulk traders at the farm gate Production space and selling space (S1, S2)
    Extension officers Provide agricultural advice and support to farmers, helping them improve practices and adapt to changes Production space (S1)
    Input suppliers Provide seeds, fertilizers, pesticides, and other agricultural inputs to farmers; some inputs are subsidized as part of a governmental policy, whereas others are not Production space (S1)
    Market queens Women traders from southern markets such as Accra and Kumasi who work in market associations around horticultural products, including tomatoes, organizing the purchase, transport, and sale of tomatoes from Burkina Faso and other regions of Ghana; a “Mother Queen” represents them at the national level, close to the King. Market queens coordinate market activities by limiting access to the market and setting selling prices Production and selling space (S1, S2)
    Leaders Interpreters and leaders who guide market queens‛ trucks to farms in Burkina Faso and facilitate bargaining between traders and farmers Production space (S2)
    Sellers Individuals who sell tomatoes at the marketplace, receiving products from offloaders (in the southern marketplaces) or from farmers directly (in the UER) Selling space (S2)
    Sorters Mainly women who sort tomatoes by quality at the farm gate, optimizing crate content for profit; they embark on trucks with leaders and market queens Production space (S1)
    Loaders Responsible for loading crates onto trucks, paid per crate by market queens Production space (S1)
    Offloaders Responsible for unloading crates at the marketplace, paid per crate by buyers or traders Selling space (S2)
    Truck drivers Paid half before and half after the trip, responsible for transporting tomatoes from farms to marketplaces Production and selling space (S1, S2)
    Consumers Ghanaian consumers, both from the UER and from southern cities such as Accra or Kumasi Consumption and selling space (S4, S2)
    District Assembly Second-level administrative subdivisions after regions; local government bodies that create and implement policies Production and selling space (S1, S2)
    Traditional Chiefs Local leaders who have influence over land allocation and community decisions Production space (S1)
    Political parties Political entities that influence agricultural policies and practices through flagship policies, legislation, and governance Farm to marketplace (S1–S4)
    Table 4
    Table 4. Consequences of climate shocks for different actors in the dry-season tomato system.

    Table 4. Consequences of climate shocks for different actors in the dry-season tomato system.

    Type of actor Consequences during a shock
    Local input supplier Financial loss due to a lack of cash flow during the stress event and by not receiving their credits back from farmers
    Farmer Financial and food stock losses if not able to replant their tomato crops or an alternative cash crop at a suitable time in the season; they have to pay back their creditors and face the lack of cash and food for a whole season
    Trader Financial losses by not receiving their credits back from the farmers, by sometimes having to provide them with a second credit to replant, and by failing in supplying their market and thus collecting their margin on the tomatoes
    Sorter Financial losses through unemployment
    Loader Financial losses through unemployment, yet they can work with other non-food products
    Leader Financial losses from credits given to farmers or traders and from the margin they would usually gain on tomatoes
    Seller Reduced tomato quantity, at higher price, eventually leading to losses and reduced income
    Consumer Higher prices for tomatoes and increased reliance on imported tomato paste
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    Home > VOLUME 30 > ISSUE 3 > Article 25 Research

    Coping with conflicts in the co-production of solid waste management services: experience with a real-world lab in India

    Pillai, S., M. Luke, and N. C. Narayanan. 2025. Coping with conflicts in the co-production of solid waste management services: experience with a real-world lab in India. Ecology and Society 30(3):25. https://doi.org/10.5751/ES-16339-300325
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    • Sruthi PillaiORCIDcontact author, Sruthi Pillai
      Centre for Technology Alternatives for Rural Areas, Indian Institute of Technology Bombay
    • Mijo LukeORCID, Mijo Luke
      Department of Humanities and Social Science, Indian Institute of Technology (IIT) Guwahati
    • N. C. NarayananORCIDN. C. Narayanan
      Ashank Desai Centre for Policy Studies, Indian Institute of Technology Bombay

    The following is the established format for referencing this article:

    Pillai, S., M. Luke, and N. C. Narayanan. 2025. Coping with conflicts in the co-production of solid waste management services: experience with a real-world lab in India. Ecology and Society 30(3):25.

    https://doi.org/10.5751/ES-16339-300325

  • Introduction
  • Methodology
  • Results
  • Discussion
  • Conclusion
  • Acknowledgments
  • Data Availability
  • Literature Cited
  • Co-production; conflict; participation; power; solid waste management
    Coping with conflicts in the co-production of solid waste management services: experience with a real-world lab in India
    Copyright © by the author(s). Published here under license by The Resilience Alliance. This article is under a Creative Commons Attribution 4.0 International License. You may share and adapt the work provided the original author and source are credited, you indicate whether any changes were made, and you include a link to the license. ES-2025-16339.pdf
    Research, part of a special feature on The Coproduction of Conflicts in Environmental Sustainability: Concepts, Methods, and Ethics

    ABSTRACT

    Co-production of knowledge and services has been employed for citizen participation to address multiple complex challenges in various policy and practice fields. By analyzing the strategies used by a collaborative initiative called CANALPY to propel an innovative campaign for solid waste management in Kerala, India, we examine the conflicting undercurrents influencing the process of co-production of services. In particular, we look at the influence of a non-governmental player in supporting service provision by the local government and an examination of the conflicts and complex power dynamics that inform the behavior of various actors. A qualitative case study approach is employed to analyze the campaign design process, the strategies employed for inducing co-production among the citizens, and the diverging interests and power of different stakeholders. The findings elucidate how CANALPY, with relatively little political power, leveraged conditioned power to align stakeholders’ interests and mitigate conflicts to support the co-production of services. Through this empirical account, we intend to lay bare the varied expressions of multiple power differentials and show how, through epistemological convergence, CANALPY paradoxically reproduces entrenched power relations and provides space to subvert them.

    INTRODUCTION

    Solid waste is one of the major challenges faced by rapidly urbanizing low- and middle-income countries. In India, the provision of solid waste management services is the responsibility of the local government (Ministry of Environment, Forest and Climate Change 2016). In response, participatory approaches such as co-production have emerged as viable strategies to enhance service delivery. Earlier studies have shown that services can be provided more efficiently by enlisting the support of the service recipients (Pestoff and Brandsen 2009). This joint production of public services by the state as well as the citizens is termed co-production (Mitlin 2008). It is defined as “a process through which inputs from individuals who are not “in” the same organization are transformed into goods and services” (Ostrom 1996:1073). Citizens contribute by supplying resources, support, and even knowledge for the delivery of services (Meijer and van der Krabben 2018). The focus on knowledge especially is important as it can contribute to improving the capabilities of the actors in coproducing the service (Watson 2014).

    Earlier empirical studies on co-production in solid waste management reveal its cultural drivers (Ben-Ari 1990), reliance on public officials and co-production thinking (Landi and Russo 2022), effectiveness as a community-based alternative to top-down regulation (Lu and Sidortsov 2019), and influence of volunteer commitment and peer pressure on household waste sorting (Xu et al. 2016). However, these studies largely depoliticize co-production, overlooking stakeholder conflicts and power dynamics (Turnhout et al. 2020). Such conflicts arise because of differences in values, knowledge, and preferences of stakeholders, uneven distribution of resources, status, and power, as well as divergent expectations (Scolobig and Gallacher 2021). Recent work examines how non-state actors navigate these challenges beyond formal governance. For instance, post-flood interventions in Wayanad, Kerala resulted in contextualized contingency planning (Koshy et al. 2022) and discretionary action by street-level bureaucrats (SLBs) optimized water supply, albeit without addressing systemic inequalities (Subramanyam 2024). In this paper we examine how a collaborative initiative called CANALPY navigates political and social tensions to enable participatory waste governance in Alappuzha. By integrating theories of power (Galbraith 1983) with co-production literature, this study contributes to the growing scholarship on co-production in waste management. Apart from advancing debates on sustainability governance, this study provides lessons for designing more inclusive, resilient social-ecological interventions.

    Context setting: solid waste management campaign in Alappuzha, Kerala

    Kerala, a densely populated state in India, lies between the Arabian Sea in the west and the Western Ghats in the east. Known for its high literacy (94% according to Census of India 2011), political engagement (Isaac 1985), and environmental consciousness (Isaac and Gopakumar 2016), Kerala’s governance framework is characterized by a highly decentralized system, where local self-governments (LSGs) are mandated to play an important role in public service delivery. In 1996, the Left Democratic Front (LDF) government launched the “People’s Campaign for Decentralized Planning,” granting local governments discretionary control over 35–40% of the state’s development funds (Heller et al. 2007). This initiative enhanced the autonomy of LSGs and institutionalized citizen participation in planning and budgeting (Isaac and Harilal 1997, Isaac 2001, Isaac and Heller 2003). As a result, urban local bodies such as municipalities are responsible for planning and implementing service delivery mechanisms, often in collaboration with both formal and informal actors.

    Urban local bodies in Kerala operate under the Kerala Municipalities Act, 1994, and the Solid Waste Management Rules, 2000. Until 2012, waste was managed through landfills, but widespread protests at 13 landfill sites prompted a shift to decentralized waste management (Ganesan 2017). The Alappuzha municipality pioneered the Nirmala Bhavanam, Nirmala Nagaram (NBNN; Clean Home, Clean City) campaign, an innovative model now recognized for its replicability across Kerala (Ganesan 2017). Its key feature was source segregation, enabling climate-friendly, affordable waste treatment that supports a circular economy and creates green jobs. The biodegradable part of the waste stream was to be treated either in the community aerobic bins provided by the municipality, or through in-home composting units or biogas plants. The non-biodegradable part was to be collected by the municipality. This idea of co-production of solid waste management services was also hailed as a participatory model with participation of households through the activity of segregation and contributing to the payment of plastic waste collection.

    Alappuzha town located in the west coast of Kerala with a population of 24,0991 (Census of India 2011; Fig. 1) was chosen as the site for a collaborative project by the Indian Institute of Technology Bombay (hereafter IIT Bombay) and Kerala Institute of Local Administration (hereafter KILA) called the CANALPY initiative Surveys conducted as part of the CANALPY revealed that the NBNN campaign had minimal impact on solid waste management (Narayanan et al. 2018). CANALPY included research staff from IIT Bombay and interns drawn from the local community. Despite the CANALPY initiative developing knowledge products and sharing insights with the municipal council, their application to sanitation interventions faced socio-political, institutional, and capacity-related barriers (Pillai and Narayanan 2022).

    These challenges led to the conceptualization of the Nirmala Bhavanam Nirmala Nagaram 2.0 (NBNN 2.0) campaign by CANALPY and the municipality. The NBNN 2.0 strategy included two activities (Fig. 2): (1) a situational assessment of the different waste types generated in households and management practices (particularly segregation) employed by the residents, and (2) the formation of participatory platforms called clusters, where councillors, resource persons such as Junior Health Inspectors disseminated responsible waste practices to the residents. The aim was to ultimately foster service co-production by encouraging dialogue and deliberation between residents and state representatives regarding shared challenges in waste management. The situation assessment survey was conducted by women’s self-help groups called Kudumbashree. Kudumbashree, introduced in 1998 as a women-oriented poverty eradication mission in Kerala, has its origin in the success of the “urban basic services for the poor” adopted in the Alappuzha municipality (Devika 2016). The survey results indicate the types of waste generated in the households (such as plastic, paper, biodegradable wet waste, etc.) and the practices adopted by the residents for its treatment and disposal, such as household composting/community composting of organic wastes and collection/segregation of inorganic wastes. Haritha Karma Sena is a team of Kudumbashree women who have been assigned the responsibility of collecting, transporting, and processing waste materials in association with local governments.

    Theoretical foundation

    The original foundational idea of the participation of actors other than the state in the production of services was by Ostrom (Ostrom et al. 1978). This concept sought to involve the public “in the execution of public policy as well as its formulation” (Whitaker 1980:241). The output of this co-production process can be both “services” or “products” (Alford 2014) and hence takes two forms: knowledge co-production and service co-production. In Science and Technology Studies (STS), Jasanoff extended the idea of knowledge coproduction to describe the mutual shaping of knowledge and social order, recognizing that knowledge both arises from and influences social structures (Jasanoff 2004). However, in the present study, co-production is used in a practical rather than analytical sense, referring to the deliberate involvement of non-scientific actors in the creation of both scientific knowledge and service provision (Van Kerkhoff and Lebel 2015).

    The process of service co-production refers to the practice of segregating, storing, and disposing of waste by either depositing it in municipal bins or composting it. This process may lead to socio-environmental changes that may empower or disempower communities, necessitating an examination of power relations among actors. The inherent nature of politics in the co-production process involves how power is allocated between actors and the results that emerge from it (Lepenies et al. 2018). A depoliticized understanding of the coproduction process reinforces already prevailing unequal social and power relations (Turnhout et al. 2020). In their more recent writings, Turnhout and colleagues (e.g., Maas et al. 2022) elaborate on differentiated responsibilities in science-policy interfaces, thus offering critical insights into the need for deconstructing the existing coproduction arrangements (Jagganathan et al. 2023). These discussions prompt a rethinking of earlier claims and highlight the importance of unpacking power dynamics to understand stakeholder motivations in engaging in the coproduction process. Literature identifies motivations for co-production, including material incentives, social rewards, expressive satisfaction, intrinsic benefits, and legal compliance (Alford 2002). Other factors include salience, which refers to citizens’ perceiving a topic as important enough to consider active engagement and weighing the investment of effort. “Personal salience” depends on the individual’s perception of how the service affects him/herself, family, or friends; “social salience” is the perceived importance of the issue to one’s neighborhood, community, or even society at large (Pestoff 2009). Other motivations include ease of participation, self-efficacy (perceived competence), and external efficacy (belief in government responsiveness; Van Eijk and Steen 2016).

    Analyzing power dynamics shaping the campaign’s execution requires studying the relations of power that influence actor behavior (Dahl 1957). Power, as a multifaceted concept, is generally defined as the capacity of individuals or groups to enact their will, shaping their social circumstances and outcomes (Barnett and Duvall 2004). It is inherently relational; an actor's power exists only in relation to others. Weber highlights this relationality, describing power as “the probability that one actor within a social relationship will carry out their will despite resistance” (Weber 1978:53). Furthermore, power is not an independent entity; it is embedded within social relations but can be wielded through the possession or threat of resources, aligning with Weberian and Dahlian perspectives of compulsory power (Ahrne 1994, Barnett and Duvall 2004). It is further consistent with Galbraith’s conceptualization of condign power, which secures desired behavior through emotional, financial, or physical threats (Galbraith 1983). The other two instruments of power proposed by Galbraith are compensatory power, which influences actors by offering symbolic, financial, or material rewards; and conditioned power, which persuades actors to engage in desired behaviors through education, cultural norms, peer influence, or advertising.

    Galbraith’s notion of three forms of power is useful in analyzing stakeholder participation (Reed 2008). Similarly, Hong (2020) explains how both conditioned power and compensatory power are helpful in addressing power relations among stakeholders in environmental decision-making processes. Integrating co-producer motivations with Galbraith’s instruments of power offers a framework for analyzing the mechanisms through which actors exercise influence in co-production campaigns. Facilitators’ knowledge, for instance, can shape negotiations and decisions within the framework of conditioned power. Toffler (1990) underscores the amplifying role of knowledge, positioning it as the most potent form of power and a fundamental ingredient in force and wealth. The mobilization of knowledge across organizational domains is thus crucial for exercising power. Figure 3 shows the analytical framework, which charts this relationship between knowledge, power, and the interests/incentives of the stakeholders.

    METHODOLOGY

    We utilize a qualitative case study, an empirical method that “investigates a contemporary phenomenon or case in depth in its own real-world context, especially when the boundaries between phenomenon and context may not be clearly evident” (Yin 2014:2). The study is based on multiple rounds of fieldwork conducted at Alappuzha Municipality, aligned with different phases of the campaign: the first round was conducted in November 2021, and the second in January 2022. This study is a part of the thesis of the first author who examined the CANALPY initiative by adopting an embedded case study approach. An embedded case study employs sub-units in order to describe or understand the whole (Yin 2014). This specific study examines the role of CANAPLY as a platform in the co-production process through an analysis of the NBNN 2.0 campaign.

    Fieldwork concentrated on seven wards out of 50 included in the campaign’s first phase, comprising four urban center wards and three peripheral wards. The primary method used was in-depth, semi-structured interviews and participant observation. In-depth interviews are one of the most important sources of case study evidence (Yin 2014). The respondents for the interviews included the municipality chairperson, councillors, health inspectors, Kudumbashree members, and residents. Except for residents, the rest of the respondents were selected from the list of stakeholders directly involved in the campaign. This was to gather their insights on decision making and implementation. Residents (co-producers) were selected based on data from the situation assessment survey, ensuring representation of individuals practicing different waste management methods. Random selection was used within this purposive frame to capture diverse approaches to waste segregation and treatment. The interview was held telephonically, and questions were framed to understand the varied interests and motives to participate in the campaign. Further, the paper analyzes three official municipality meetings and 10 cluster meetings held at the ward level. Participant observations were supplemented by pamphlets and notices distributed as part of the campaign.

    The data collected are corroborated with information from secondary sources such as survey results from previous studies and information from the situation assessment conducted as part of the campaign. It is important to note that the survey preceded the fieldwork for this study. Moreover, the CANALPY members interviewed for this paper did not overlap with those who prepared the questionnaire for the survey. The interview and participant observation data was transcribed and analyzed by thematic analysis (Braun and Clarke 2006). Themes emerged from the research questions and from the analytical framework developed for the research. The analysis explores participant demographics, the nature of their involvement, stakeholder roles, and motivations. Details of the data collected are presented in Table 1.

    RESULTS

    Strategic execution of NBNN 2.0: leveraging low-hanging fruit for political buy-in

    The NBNN 2.0 campaign had two key activities: a preliminary survey and cluster meetings. The preliminary situational assessment was conducted by the municipality, with CANALPY designing the questionnaire and Kudumbashree volunteers administering it to understand the current status of solid waste management practices. Survey results presented in Figure 4 indicated that the majority of the residents admitted to disposing of the waste on land around their premises. A small minority of residents segregated their waste and used different waste management methods to treat the biodegradable fraction of the waste.

    One of the conflicts that had arisen earlier during CANALPY’s work was the expectation of swift results by the elected representatives (Pillai and Narayanan 2022). The absence of immediate and tangible impact led to waning interest and, ultimately, withdrawal of political support. To address this, CANALPY strategically restructured the campaign to leverage “low-hanging fruit,” achievable and, more importantly, familiar interventions that aligned with the political interests of the elected representatives. The campaign’s success was thus determined by the achievement of two specific criteria: (1) all households adopting at least one of three waste segregation methods, i.e., kitchen bins (bio-bins) distributed by councillors, biogas plants, or community composting units; and (2) households handing over plastic waste to Haritha Karma Sena through a user-fee model. These were chosen because they proved to be politically and logistically viable during NBNN 1.

    The second activity was cluster meetings, which are participatory forums where councillors reached out to the residents to encourage the adoption of responsible waste management practices. The formation of participatory structures for citizen engagement within local policy making plays a crucial role in the success of co-production (Chaebo and Medeiros 2017, Alonso et al. 2019). The clusters, however, were not only designed for one-way information dissemination. According to a CANALPY team member, “Cluster meetings were supposed to be opportunities for residents to flag their concerns regarding waste management in their wards to their councillors.”

    The councillors divided each ward into clusters of 50 households, and participation in meetings was ensured through messaging in WhatsApp groups and personal calls from councillors or cluster coordinators. In the words of 35-year-old Rajesh, a cluster coordinator, “We pass on the information about the meetings and other campaign activities through the WhatsApp group, we circulate the awareness videos about the waste segregation from different parts of the state, it helps to educate the cluster members.”

    Examining cluster-level meetings and stakeholder engagement

    The organizational structure of the campaign details the different stakeholders who were involved in the campaign (Fig. 5). Table 2 details the roles and responsibilities of the formal and informal actors involved in the campaign. Cluster-level meetings were organized by designated coordinators and facilitated by resource persons from the municipality, such as Junior Health Inspectors. Cluster meetings were intended to be an inclusive platform for deliberation irrespective of caste, class, and gender.

    However, an analysis of the meetings showed abysmal attendance levels with limited representation from men. A majority of the participants consisted of self-employed Kudumbashree women and party-affiliated men. Kudumbashree’s organizational skills, accountability, and accessibility make them ideal participants for any program or activity, prompting councillors to rely on them for populating cluster meetings. Williams et al. (2015) highlight that the selection of Kudumbashree participants in government programs often reflects entrenched clientelistic relationships, wherein state actors leverage these networks to sustain political influence. Further, interviews revealed that Kudumbashree members perceive engagement in municipal activities as a means of social mobility and, in some instances, a pathway to political advancement. Their participation, therefore, does not necessarily indicate an intrinsic commitment to environmental concerns or sustainable waste management; rather, it appears to be primarily driven by external rewards, political visibility, and perceived social capital.

    These external rewards were identified as primary motivators for other stakeholders involved in the process as well. Cluster coordinators, tasked with organizing cluster-level meetings, are selected by councillors from accessible individuals such as the party cadre. They have strong political ambitions and view their role as an opportunity to establish political credibility. However, their, as well as Kudumbashree members’ participation is largely passive with no substantial contribution to subsequent deliberations or discussions. This reveals a pattern wherein attendance in these meetings is part of their everyday transactions with local politics. It clearly shows that participation is limited to those who already cooperate with various municipality activities and is ineffective in generating public demand for the campaign.

    Although initially designed to be inclusive spaces for deliberations between residents and powerful actors such as elected representatives, clusters were relegated to being performative spaces with very narrow impact, if any. In the absence of participation by the target residents, it becomes imperative to understand the underlying drivers of the process of co-production. To understand the same, we sought to explore diverse stakeholder interests and power dynamics affecting co-production behavior.

    Power dynamics shape stakeholder interests in NBNN 2.0

    Understanding factors that drove co-production will require an examination of the interests of diverse stakeholders and the power dynamics that shaped their participation. Residents, the primary stakeholders in the process, had diverse motivations for engaging in waste segregation. The preliminary situation analysis survey showed that some of the residents were already involved in the segregation of waste. Although the majority claimed to engage in co-production for personal and social salience, some admitted that participation was not always voluntary. External pressures such as coercion from councillors and fear of sanctions played a role in shaping their behavior.

    Although councillors’ primary motivation for leading the campaign was their political aspirations, many elected representatives reported that their experiences in NBNN 1 inspired their participation in NBNN 2.0. Similarly, officials who took an interest in the campaign were either associated with waste management campaigns in other parts of Kerala or were generally committed to Kerala’s decentralization campaign. Others participated in the campaign in order to ensure a good service record. As elaborated in above, other stakeholders engaged with the campaign primarily for broader political and electoral opportunities.

    The councillors strategically employed condign power, compensatory, and conditioned power to influence residents and other stakeholders. On the one hand, they used their authority to mandate compliance through coercion, often warning residents about penalties or loss of municipal services if waste segregation norms were not followed; on the other, they reinforced desirable behavior by acknowledging compliant households in ward meetings and distributing subsidized bio-bins. Further, through the dissemination of educational videos, WhatsApp campaigns, and strategic messaging, conditioned power was wielded to create a perception that “responsible citizens” segregate their waste.

    Although powerful actors like councillors used different instruments of power to encourage specific behavior, the CANALPY team exercised conditioned power to persuade the chairperson and councillors. To ensure the political buy-in of councillors, apart from leveraging “low-hanging fruit,” CANALPY devised a media campaign that employed newspapers and social media for outreach and publicity, which gave limelight to the chairperson and councillors, who thus remained the face of the campaign. This visibility and subsequent political mileage incentivized the political elite to lead the campaign. Ultimately, different actors deployed distinct instruments of power to facilitate co-production: elected representatives and bureaucrats used condign power whereas CANALPY employed conditioned power to foster citizen engagement in service co-production.

    DISCUSSION

    Although the original intention of this study was to examine the conflicts arising in the design of a co-production campaign, through the course of the work, we have unpacked how power dynamics and stakeholder motivations shape the process of coproduction. The findings demonstrate how CANALPY circumvented the conflicts that emerged during the campaign by leveraging their learnings from previous collaborative efforts with the municipality. The main conflict was in designing the campaign in a manner that meets the expectations of the elected representatives. Interviews revealed that a majority of councillors viewed the campaign as an opportunity to consolidate their political influence rather than a means to improve waste management. It was thus crucial to leverage this interest to ensure the success of the campaign. Naturally, the elected representatives became the most powerful drivers of the co-production process, and findings illustrate how they employed different types of approaches (Fig. 6) to induce coproduction.

    A central theme emerging from the empirical findings is the role of power in shaping participation in co-production. Councillors and the chairperson, as key political actors, leveraged different forms of power, condign, compensatory, and conditioned power (Galbraith 1983), to ensure compliance with waste segregation practices. The presence of powerful actors in the campaign process, however, raised concerns about potential conflicts around the varied interests they represented. Engaging with influential actors such as elected representatives shaped the behavior of other stakeholders, often reinforcing existing power dynamics. This dynamic may result in political leaders who have access to opportunities and influence abusing their power and eventually impeding the process of coproduction (Siame and Watson 2022). Although CANALPY imagined cluster-level meetings as invited spaces wherein co-production transfers some power from state actors to lay actors, thus giving them a legitimate voice (Bovaird 2007), inadvertently, they also reproduced existing power differentials in society as the relationship between different stakeholders continued to function within traditional power dynamics.

    Although the campaign has demystified how power operates through actors to drive it forward, it then becomes crucial to deliberately shift power by envisioning new spaces for participation that extend beyond performative spaces such as cluster meetings. Creating platforms where individuals can collaborate, reflect, and act at their own pace, akin to the concept of management councils as described by Gutberlet (2015), is essential for the redistribution of power and the emergence of meaningful participation. This highlights the importance of developing strategies that consider local specificities and structural factors such as the heterogeneity of the community while ensuring space for dialogue and negotiation (Pestoff 2009, Turnhout et al. 2020).

    Additionally, facilitating community capacity-building activities through adequate investment in training public officials will lead to the fostering of an institutional culture that is receptive to the process of co-production (Steiner et al. 2022). Our study shows how municipal officials, political representatives, and intermediaries negotiate power and incentives to sustain waste segregation, reinforcing that co-production is deeply embedded in existing governance structures. Insights from recent studies by Koshy (2022, 2024) and Subramanyam (2024) also highlight how governance adapts through informal mechanisms and discretionary actions. Koshy’s work on actor ecosystems and blurred organizational boundaries in post-disaster governance aligns with our findings on CANALPY’s role in Kerala’s decentralized system. Subramanyam’s study on discretionary governance in Tamil Nadu underscores the influence of non-state actors and frontline workers in shaping service delivery beyond formal mandates.

    Another critical factor that contributed to the design of the campaign was the preliminary information about the status of waste management. This formed the basis on which the CANALPY team and the chairperson convinced other stakeholders to participate in the co-production process. The strategic alignment of this information with the interests of political stakeholders facilitated the expansion of co-production. This is in line with earlier findings, which indicate that aligning the sustainability experiments with government expectations is instrumental in securing support and ensuring long-term sustainability (Wang et al 2024). Our analysis also highlights the central role of political actors to give teeth to coproduction, aligning with findings from Shanghai where local governments incentivize participation of residents and share resources to sustain and scale initiatives (Arantes et al. 2020). However, unlike this case of government-led collaboration, our work paints a contrasting picture of an NGO-initiated partnership.

    Engaging with previous scholarship that foregrounds the political implications of co-production (Lepenies et al. 2018, Turnhout et al. 2020) showed the need for unpacking structural dynamics in power-laden institutional contexts. However, that can risk overdetermining the agency of local actors. Although it is true that power asymmetries between actors exist as in many other cases of service coproduction (for example, Chatterjee and Kundu 2022), contingent strategies and improvisations, such as the use of scientific knowledge and contextual translation by CANALPY to further service coproduction, can partially subvert dominant power structures even within constrained political environments. This is in line with earlier findings from the literature where such platforms act as arenas for inclusion of diverse knowledge systems and voices by “gate-keeping” or controlling the participants, their roles, and the scope of their involvement (Jagannathan et al. 2023). This highlights the operation of conditioned power, provocatively conceptualized as the power exercised by the powerful in a social order so as to satisfy their interests by letting others think that those ends are also theirs (Caporaso and Levine 1992). In other cases, in NGO-led initiatives such as this, government support emerges only after an initiative stabilizes, with the role of the government shifting to offering significant political and financial support (Wang et al. 2024). Here, we explicitly document how the NGO strategically garners this support through persuasion and knowledge, leveraging the instrument of conditioned power.

    One of the limitations of this work is the inadequate engagement with the motivation of the co-producers. The theoretical section dwelt on the motivations for co-production, such as material incentives, social rewards, expressive satisfaction, salience, and self, as well as external efficacy. The focus on power dynamics and stakeholder engagement has limited the discussion to the interests of political and bureaucratic representatives. Although empirical results indicate that some residents engaged in segregation because of personal or social salience, coercion from councillors, and fear of sanctions, this study has not sufficiently unpacked the key drivers of their behavior. This highlights a gap in distinguishing between voluntary and externally influenced participation and calls for further research to examine the nuances of co-producers’ intrinsic and extrinsic motivations.

    CONCLUSION

    Solid waste management faces significant challenges in developing countries because of a lack of resources and complex power dynamics among decision makers and other stakeholders. This study highlighted the potential of co-production in addressing these challenges by promoting collaboration between citizens and the state. Our analysis of the NBNN 2.0 campaign in Alappuzha reveals that although co-production is often framed as a means to enhance participatory governance, it is deeply embedded in existing power hierarchies. CANALPY’s use of conditioned power helped align political motivations but failed to dismantle entrenched power differentials, as seen in the ineffective cluster-level meetings. This study thus highlights how epistemological convergence both reinforces and subverts existing power structures.

    The findings have significant implications for the governance of social-ecological systems, especially for similar contexts from the Global South, it holds valuable lessons on power dynamics, governance-NGO interactions, and formal-informal collaborations for service provision. First, they illustrate that the sustainability of co-production initiatives depends on technical feasibility as well as the ability of the collaborative initiative to understand the political and institutional contexts in which they operate. This will aid the non-government organizations in playing a crucial role in bridging governance gaps by translating knowledge into action and facilitating engagement between political and civic actors. Second, the findings suggest that fostering genuine citizen engagement requires moving beyond invited spaces of participation (such as cluster meetings) to more transformative modes of deliberation that allow for contestation and negotiation. The strategic approach employed by CANALPY of employing conditioned power to align the motivations and interests of political stakeholders was crucial in navigating the conflicts and ensuring the success of the campaign. Nevertheless, the failure of the cluster-level meetings shows that this conditioned power does little to dismantle the entrenched power differentials. Finally, the study highlights the need for sustained institutional support and capacity-building mechanisms to ensure the longevity and equity of co-production processes. The sustainability of the process of coproduction is thus incumbent upon strong institutional support, community capacity building, and continual engagement of all stakeholders. These insights can be valuable for designing, scaling up, and institutionalizing co-production efforts in other regional and urban contexts, leading to effective and, more importantly, equitable service delivery.

    Being attentive to the ways in which scientific and societal discourses are intertwining and interpreted is important if transformative change is to occur. The intersection of governance, NGOs, and informal collaborations provides opportunities for reshaping service provision and sustainability practices, especially in the resource-constrained Global South. Designing participatory governance structures that enable marginalized voices to shape decision making and integrating informal community networks with formal governance institutions can enhance service delivery resilience and sustainability. However, it must be approached critically because, in practice, these participatory arrangements may obscure structural inequalities and shift responsibility to citizens without corresponding authority. By recognizing these interdependencies and acknowledging their constraints and uneven burdens, future co-production initiatives can more effectively harness local knowledge, foster equitable participation, and develop adaptive governance frameworks that enhance long-term resilience.

    RESPONSES TO THIS ARTICLE

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    ACKNOWLEDGMENTS

    We wish to acknowledge the support of Alappuzha Municipality and CANALPY team members for their participation in this research.

    Use of Artificial Intelligence (AI) and AI-assisted Tools

    We did not use any generative AI or AI-assisted technology for the preparation of this manuscript.

    DATA AVAILABILITY

    Data/code sharing is not applicable to this article because no data/code were analyzed in this study.

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    Corresponding author:
    Sruthi Pillai
    msruthipillai@gmail.com
    Fig. 1
    Fig. 1. Location of Alappuzha, Kerala, India. Source: Jishnu A. M.

    Fig. 1. Location of Alappuzha, Kerala, India. Source: Jishnu A. M.

    Fig. 1
    Fig. 2
    Fig. 2. <em>Nirmala Bhavanam, Nirmala Nagaram</em> (NBNN; Clean Home, Clean City) campaign strategy. The preliminary situation assessment survey conducted with the municipality led to insights on the current waste management practices of residents. Cluster-level meetings aimed at disseminating better waste management practices with the ultimate objective of facilitating service co-production by encouraging citizens to actively participate in waste segregation.

    Fig. 2. Nirmala Bhavanam, Nirmala Nagaram (NBNN; Clean Home, Clean City) campaign strategy. The preliminary situation assessment survey conducted with the municipality led to insights on the current waste management practices of residents. Cluster-level meetings aimed at disseminating better waste management practices with the ultimate objective of facilitating service co-production by encouraging citizens to actively participate in waste segregation.

    Fig. 2
    Fig. 3
    Fig. 3. The analytical framework to understand power and politics in co-production. While actors are motivated by their interests and incentives, they employ different types of power to invoke different types of motivation, such as salience, efficacy, and material or expressive incentives, in other actors.

    Fig. 3. The analytical framework to understand power and politics in co-production. While actors are motivated by their interests and incentives, they employ different types of power to invoke different types of motivation, such as salience, efficacy, and material or expressive incentives, in other actors.

    Fig. 3
    Fig. 4
    Fig. 4. Situational assessment survey results.

    Fig. 4. Situational assessment survey results.

    Fig. 4
    Fig. 5
    Fig. 5. Organizational Structure of the NBNN 2.0 campaign. NBNN = <em>Nirmala Bhavanam, Nirmala Nagaram</em> (Clean Home, Clean City).

    Fig. 5. Organizational Structure of the NBNN 2.0 campaign. NBNN = Nirmala Bhavanam, Nirmala Nagaram (Clean Home, Clean City).

    Fig. 5
    Fig. 6
    Fig. 6. Power dynamics between different stakeholders: different actors employed different types of power to elicit desired behaviors from other actors. Being an informal actor, CANALPY could only employ conditioned power, but the councillors, on account of their legitimacy and authority, could employ all three forms of power on other actors.

    Fig. 6. Power dynamics between different stakeholders: different actors employed different types of power to elicit desired behaviors from other actors. Being an informal actor, CANALPY could only employ conditioned power, but the councillors, on account of their legitimacy and authority, could employ all three forms of power on other actors.

    Fig. 6
    Table 1
    Table 1. Data, description, and sources.

    Table 1. Data, description, and sources.

    Data Rationale/purpose Description
    Semi-structured interviews (n = 20) were gathered using purposive sampling + 1 focus group discussion with 5 participants. To understand the participants’ points of view, goals, and expected outcomes of the campaign. Twenty-five individual interviews of seven Councillors, five CANALPY team members and eight Kudumbashree volunteers, and a focus group discussion of five Haritha Karma Sena Workers.
    Participant observation. To gain an understanding of the process of cluster meetings and the nature of interaction between different stakeholders. Field notes from cluster meetings and municipality meetings held as part of Phases 1 and 2 of the campaign. Authors participated as observers and engaged in informal conversation with the residents.
    Interview with co-producers. To understand how the residents as co-producers interpreted the campaign and their motivation for engaging in co-production. Thirty-eight telephonic interviews were conducted to understand the perspective of residents and to analyze conflicts between the strategy employed and actual implementation on the ground.
    Table 2
    Table 2. Stakeholders with their roles and responsibilities.

    Table 2. Stakeholders with their roles and responsibilities.

    Actor Role category Responsibilities
    Municipal chairperson Formal Provide strategic oversight, coordinate municipal departments, ensure execution, and resolve stakeholder conflicts
    Municipal councillors Formal Promote household participation, allocate resources, and ensure compliance with waste segregation norms
    Junior health inspectors Formal Leading knowledge dissemination during cluster-level meetings
    CANALPY Informal Provide strategic oversight, coordinate municipal departments, ensure execution, and resolve stakeholder conflicts
    Kudumbashree Formal Engage with the community, facilitate household waste segregation, and participate in cluster meetings
    Haritha Karma Sena Formal Collect, transport, and process segregated waste while encouraging proper waste disposal practices
    Cluster coordinators Informal Plan the campaign strategies and organize the cluster-level campaign activities
    Disseminate relevant information to residents
    Residents Informal Participation in the meetings and support for co-production by segregating waste at the source
    Volunteer clusters Informal Act as intermediaries between residents and municipal authorities
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