Erik Meijaard1,2*
Nabillah Unus1
Thina Ariffin1
Rona Dennis1
Marc Ancrenaz1,3
Serge Wich4
Sven Wunder5,6
Chun Sheng Goh7,8
Julie Sherman9
Matthew C. Ogwu10Johannes Refisch11Jonathan Ledgard12
Douglas Sheil13†
Kimberley Hockings14†- 1Borneo Futures, Bandar Seri Begawan, Brunei
- 2Durrell Institute of Conservation and Ecology (DICE), School of Anthropology and Conservation, University of Kent, Canterbury, United Kingdom
- 3HUTAN-Kinabatangan Orangutan Conservation Programme (HUTAN – KOCP), Sandakan, Malaysia
- 4School of Biological and Environmental Sciences, Liverpool John Moores University, Liverpool, United Kingdom
- 5European Forest Institute, Barcelona, Spain
- 6Center for International Forestry Research, Lima, Peru
- 7Jeffrey Sachs Center on Sustainable Development, Sunway University, Kuala Lumpur, Malaysia
- 8Harvard University Asia Center, Cambridge, MA, United States
- 9Wildlife Impact, Portland, OR, United States
- 10Goodnight Family Sustainable Development Department, Appalachian State University, Boone, NC, United States
- 11Great Apes Survival Partnership, United Nations Environment Program, Nairobi, Kenya
- 12Artificial Intelligence Center, Czech Technical University, Prague, Czechia
- 13Forest Ecology and Forest Management Group, Wageningen University and Research, Wageningen, Netherlands
- 14Center for Ecology and Conservation, University of Exeter, Penryn, United Kingdom
Non-human great apes – chimpanzees, gorillas, bonobos, and orangutans – are threatened by agricultural expansion, particularly from rice, cacao, cassava, maize, and oil palm cultivation. Agriculture replaces and fragments great ape habitats, bringing them closer to humans and often resulting in conflict. Though the impact of agriculture on great apes is well-recognized, there is still a need for a more nuanced understanding of specific contexts and associated negative impacts on habitats and populations. Here we review these contexts and their implications for great apes. We estimate that within their African and South-East Asian ranges, there are about 100 people for each great ape. Given that most apes live outside strictly protected areas and the growing human population and increasing demand for resources in these landscapes, it will be challenging to balance the needs of both humans and great apes. Further habitat loss is expected, particularly in Africa, where compromises must be sought to re-direct agricultural expansion driven by subsistence farmers with small fields (generally <0.64 ha) away from remaining great ape habitats. To promote coexistence between humans and great apes, new approaches and financial models need to be implemented at local scales. Overall, optimized land use planning and effective implementation, along with strategic investments in agriculture and wildlife conservation, can improve the synergies between conservation and food production. Effective governance and conservation financing are crucial for optimal outcomes in both conservation and food security. Enforcing forest conservation laws, engaging in trade policy discussions, and integrating policies on trade, food security, improved agricultural techniques, and sustainable food systems are vital to prevent further decline in great ape populations. Saving great apes requires a thorough consideration of specific agricultural contexts.
1 Introduction
Agricultural expansion is the leading cause of biodiversity loss, with global cropland estimated at 1,244 Mha in 2019 (Potapov et al., 2022) and predicted to expand further by 193–317 Mha by 2050, mainly in Africa (Schmitz et al., 2014). This expansion will reduce available habitat for 87.7% of the 19,859 terrestrial vertebrate species recently reviewed by Williams et al. (2021), with 1,280 species losing >25% of their remaining range. Balancing the demands for crops and conservation is one of the biggest challenges of the 21st century (Dudley and Alexander, 2017), especially in the tropics, where species diversity is high, and large natural ecosystems are declining due to human impacts (Cincotta et al., 2000; Pendrill et al., 2022). The impact of agriculture on non-human great apes (further referred to as “great apes”) in the Asian and African tropics is of particular concern, with chimpanzees, bonobos, Western and Eastern gorillas, and three species of orangutans all in decline and threatened with extinction within the coming decades (Figure 1, for scientific names see Table 1). The distribution and density of these species are primarily determined by habitat availability, disease, killing for meat and other purposes, and people’s attitudes to sharing landscapes with great apes. Despite national legislation legally protecting these species in all 23 countries they occur in, the threat to their survival remains high (Caldecott and Miles, 2006; Bettinger et al., 2021).
Figure 1 (A) African great ape subspecies ranges in relation to the distribution of crops expressed as majority crop per 10*10 km grid cell (You et al., 2017). (B) Asian great ape subspecies. Population estimates from Rainer et al. (2020) and ranges based on IUCN Red List data for individual species.
Table 1 Great ape taxa, the number of people within the great ape ranges (Schiavina et al., 2022), the primary drivers of forest cover loss (Laso Bayas et al., 2022), and main crops in great ape ranges (Meijaard et al., 2021).
The remaining great apes (750,000-1,250,000, see Figure 1) share their distribution ranges with around 97 million people (1 great ape per 77-129 people, see Supplementary Materials and Table 1). In simple terms, one great ape shares resources with 100 humans, mainly in countries with high human population growth and poverty (i.e., income of less than US$2 per day), and low food security. For instance, according to World Bank data, the Democratic Republic of the Congo (DRC) has a 2.9% annual population growth rate, which could double the number of people living alongside great apes in 25 years. Some of the great ape range countries are also those with the highest levels of undernourishment: 21% of the Sub-Saharan people were undernourished in 2020 (The World Bank, 2022a). Thus, there is an urgent need for increased local food production and more equal distribution of food to improve food availability, affordability, and security. Growing human populations and a drive for economic development, alongside growing international demand, remain key drivers of deforestation (Busch and Ferretti-Gallon, 2017) and therefore great ape habitat loss.
The threats to great apes related to agriculture include habitat loss and fragmentation due to agricultural expansion, the resulting genetic factors related to small and isolated populations, agriculture-related diseases, as well as the human-great ape conflict, and ape killing, capture, and trade (Figure 2). In terms of agricultural expansion, we focus on crops rather than livestock, because in the orangutan ranges livestock-related forest loss is rare, while, in Africa, such losses are concentrated in the drier parts where great apes generally do not occur (although chimpanzee habitat in Tanzania, Senegal, and Mali is a local exception). Maize (Zea mays L.), rice (Oryza spp.), millet (various species), and cassava (Manihot esculenta Crantz) are the main crops of concern (for details see Tables S1–S3). These are mostly grown in smallholder, subsistence agriculture contexts (Table 1), with fields typically <0.64 ha in size (Lesiv et al., 2019), and further field size reduction ongoing (Abraham and Pingali, 2020). Rice, maize, and cassava show the most rapid expansion, while other crops such as sesame (Sesamum indicum L.), sunflower (Helianthus annuus L.), cotton (Gossypium L.) and okra (Abelmoschus esculentus (L.) Moench) have expanded but use up less land (FAOSTAT, 2023). African oil palm (Elaeis guineensis Jacq.) is another crop that has been a driver of deforestation, especially in Southeast Asia’s orangutan ranges (Table S4), with concerns about its expansion in Africa and potential impact on great apes (Linder, 2013; Wich et al., 2014). While the media has extensively covered the effects of industrial oil palm expansion on great apes, there has been relatively little scrutiny on the impacts of other crops (Jayathilake et al., 2021).
Figure 2 Causal transmission chain of (negative) change between human expansion in land use and the fate of the great apes (referred to as “apes”).
There is considerable variation in the type of crops grown across the great ape range (Supplementary Materials). Most African great apes reside in tropical evergreen forests, but some populations are also found in deciduous woodland and drier savannah-dominated habitats interspersed with gallery forests. The crops grown in these areas are adapted to equatorial fully humid, monsoonal, summer dry, and winter dry conditions (Kottek et al., 2006). The regions primarily cultivate annual crops, although there are also perennial crops such as oil palm, tree crops, and cacao (Table 2). The use of crop areas by great apes for feeding or dispersal, and the level of persecution they face for consuming different crops, vary depending on the type of crop cultivated and species ecology (Supplementary Materials). Soil fertility may also influence great ape presence, with areas in Borneo that have low soil fertility and are poorly suited to agriculture, traditionally being used by nomadic hunter-gatherer people who likely hunted out orangutans in the past (Meijaard, 2017). It remains unclear whether this also applies to Africa, although the more fertile parts, such as volcanic mountain slopes (see, e.g., Hengl et al., 2021) seem to retain species such as mountain gorillas.
Table 2 Typology of main crops that occur in great ape ranges and are likely to cause most great ape habitat loss.
Only some areas of the remaining great ape habitat are formally protected. For example, 83% of chimpanzees in West Africa (Heinicke et al., 2019) and about 80% of central chimpanzees and western gorillas in Central Africa reside outside protected areas (Kormos et al., 2003; Brncic et al., 2015; Tweh et al., 2015; Strindberg et al., 2018). Additionally, about 50% of orangutans in Indonesian Borneo reside outside protected areas (Meijaard et al., 2022b). These unprotected habitats are under particular threat from agricultural expansion, though even protected areas can be vulnerable – depending on management, and the extent to which community needs are integrated into protected area management. Overall, understanding the distribution and ecology of great apes is crucial in understanding the threat posed by agriculture.
The different characteristics of the fourteen great ape species and subspecies (Table 1, Supplementary Materials), the different regions of the world in which they occur, and the different agricultural crops that may threaten their habitats or provide some ecological opportunities to them (Table 2), result in a complex picture regarding the relationship between agriculture and great apes. This is further confounded by the scales at which crops are produced (e.g., smallholder or industrial scale), growth types (annual or perennial, monoculture or inter-cropped) or whether crops are produced for subsistence or cash-income purposes. Here we review the literature on great apes and agriculture. Because of the complex nature of the topic and the often qualitative evidence presented in published sources, we use literature review with narrative synthesis to generate insights about the apes and agriculture interface (Grant and Booth, 2009). We searched the scientific literature for papers on great apes in agricultural contexts using species names as search terms, combined with agriculture-related search terms, but did not conduct a formal quality assessment. Trends in land use associated with various crops were determined using data provided by the United Nations Food and Agriculture Organization. Our objectives are to 1) assess the dominant crops and food systems in the ranges of the 14 great ape species and subspecies; 2) identify antagonistic and synergistic co-occurrences; 3) understand economic and political factors that might influence future agricultural developments; and 4) provide recommendations towards improved co-existence between apes and agriculture. We hope to clarify how future agricultural developments are likely to affect different great ape taxa, and what can be done to minimize negative impacts.
2 Key agricultural trends where apes and crops converge
In Africa, agricultural production mainly serves domestic consumption with few crops generating export revenues (Rakotoarisoa et al., 2012). Smallholder farming dominates, although a transition to business-oriented processes is underway (Mukasa et al., 2017; Giller, 2020). Farms still struggle to provide food security or living incomes. Production is expected to increase (Sanchez, 2002; Pendrill et al., 2022; Potapov et al., 2022), putting further pressure on land, especially in Ghana, Ivory Coast, Benin, Nigeria, and Cameroon (Halpern et al., 2022). Infrastructural development related to extractive industries (Weng et al., 2013) is linked to agricultural growth corridors (Independent Science and Partnership Council, 2016), impacting areas of high biodiversity (Laurance et al., 2015).
Agricultural expansion on Borneo and Sumatra has led to major forest loss since the 1970s (Wilcove et al., 2013). These tropical islands are highly suitable for the cultivation of crops such as oil palm, with rice, rubber (Hevea brasiliensis Müll. Arg.), maize, coconut (Cocos nucifera L.), and coffee (Coffea arabica L.) also grown (Table S4). Oil palm agriculture is dominated by large-holders, but while there is more industrial-scale agriculture compared to African great ape ranges (Table 1), forest loss has declined recently due to improved governance of this sector (Gaveau et al., 2019; Gaveau et al., 2022). Nevertheless, soil impoverishment and economic factors drive smallholder farmers to clear forests (Duffy et al., 2021), especially low nutrient peat swamp forests that are important for orangutans (Meijaard et al., 2010).
Across Sub-Saharan Africa and South-East Asia, agricultural expansion is leading to significant changes in land use patterns, with certain crops showing particularly rapid rates of growth. Cassava, oil palm, and rubber have been the crops with the greatest regional expansion rates (Table 2). Meanwhile, land under maize is also expanding, and if current regional trends continue, it may approach equivalence with the area under rice within the next decade. Two other crops, yams (Dioscorea spp.) and plantain (Musa spp.) have also seen significant increases in area between 2010 and 2021, with respective growth rates of 87.0% and 55.2% (FAOSTAT, 2023).
There is considerable variation in crop distribution across different regions. In Central Africa, for instance, which is home to bonobos, chimpanzees, and Western gorillas, the largest areas are allocated to cassava, maize, groundnuts (Arachis hypogaea L.), sorghum (Sorghum bicolor L. Moench), and rice (Table S1). Meanwhile, in West Africa, which is home to chimpanzees and Cross-River gorillas, sorghum, maize, and cow peas dominate (Table S2). While the effects of climate change on crop distribution are unclear, it is likely that areas with rain-fed agriculture and limited economic and institutional capacity to respond to climate variability and change, such as some parts of West Africa, will be negatively impacted through yield losses (Sultan and Gaetani, 2016). Such losses could increase pressure on the remaining forested areas where great apes live. In Borneo, predicted reductions in rainfall and increases in temperature (McAlpine et al., 2018) are likely to limit areas suitable for crops such as oil palm, which is vulnerable to prolonged drought, and reduce available orangutan habitat (Struebig et al., 2015).
Great apes react differently to reduction in forest habitats and changing foraging opportunities and threats (see Supplementary Materials for short species ecology reviews). The species are primarily adapted to a plant diet – with meat consumption by chimpanzees being an exception (Fahy et al., 2013) – and may target crops in fields or fruit and trees in orchards and plantations, especially when wild foods are scarce, but also because these may be preferred, since they are highly nutritious and easy to access (Hockings and Humle, 2009; Hockings et al., 2009; Campbell-Smith et al., 2011; Hockings and McLennan, 2012; Seiler and Robbins, 2016). Great apes and humans also share the need for water (Box 1).
Preliminary studies indicate that individuals in some great ape species change their behavior over time to human-dominated landscapes (Hockings et al., 2015), changing food items as they learn what is edible and learning to navigate agricultural lands (McLennan and Hockings, 2014; Ancrenaz et al., 2015; McLennan et al., 2021). These behaviors are often maladaptive, as the nutritional benefits can be outweighed by the costs of increased mortality through accidental snaring, retaliatory killings, and disease. As species with low reproductive outputs, retaliatory killings of apes by humans in response to crop consumption are unlikely to be sustainable. Disagreements between different human groups over how to manage problematic great ape behavior can follow (Campbell-Smith et al., 2011; Hockings and McLennan, 2012).
Box 1. The crucial role of access to water for great apesn.
Apes obtain water from their food and by drinking surface water or water collected in tree holes, sometimes with the use of leaf tools, with some communities of chimpanzees digging wells (Figure 3). However, agriculture and climate change have reduced the availability of water (Akpabio, 2007), affecting great apes’ health, behavior, and social interactions. For instance, apes in sub-Saharan Africa are facing water scarcity due to increased competition and climate change effects (Vise-Thakor, 2022). Reduced water sources force great apes to drink from fewer shared drinking spots, which increases disease risk (Wright et al., 2022) and the likelihood of aggressive interactions with people, especially children. The proximity of water sources for agricultural areas can also lead to contamination of water sources with pesticides (Masi et al., 2012; Shively and Day, 2015; Sharma et al., 2016). Great apes might be able to adapt to these challenges by developing new behaviours or adapting existing ones, such as well digging (Kalan et al., 2020; Péter et al., 2022), but conservation planning must focus on ensuring safe access to water for great apes as part of forest protection.
Figure 3 Adult male chimpanzee at a drinking hole at Cantanhez National Park. Reprinted with permission from Joanna Bessa (Cantanhez Chimpanzee Project).
3 Reducing antagonistic co-occurrences between great ape conservation and agriculture
Great apes can coexist with humans in shared landscapes, but local attitudes towards them determine whether this is beneficial or harmful. Coexistence requires humans and wildlife to co-occur (Harihar et al., 2013), with tolerable risks to both, and should be sustainable (Carter and Linnell, 2016). Some sites have shown co-adaptation between chimpanzees and smallholder agriculture (Halloran, 2016; Bersacola et al., 2021; McLennan et al., 2021), while orangutans survive in forest fragments in Malaysian oil palm landscapes because people accept their presence (Ancrenaz et al., 2021). People in the latter landscape are generally not concerned about orangutans or crop losses, and orangutans are generally safe, although it is unclear if these fragmented populations will remain viable in the long-term (Oram et al., 2022). Conservation planning for great apes needs to consider whether agricultural expansion is driven by poverty and if killing of great apes may continue, or if more stable conditions can be achieved.
Preventing agricultural expansion is the best way to minimize negative impacts on great apes, but this can be difficult in regions with undernourishment and poverty (Meijaard et al., 2022a). Areas of poverty often coincide with relatively good forest protection (Busch and Ferretti-Gallon, 2017), but transitioning to middle-income levels may accelerate agricultural development and pose a threat. Reducing poverty without deforestation requires greater stakeholder engagement (Garcia et al., 2020), such as involving communities in forest enterprise (Santika et al., 2019), although the broader applicability of such models across great ape ranges remains unclear. Also, even when deforestation rates can be reduced, reducing poaching rates is challenging and requires long-term financing (Sandker et al., 2009).
Efforts to reduce forest loss and poaching rates whilst alleviating poverty could help reduce pressures on great ape populations and habitats as economies develop, i.e., the forest transition (Mather and Needle, 1998). In Africa, deforestation is thought to be positively related to real Gross Domestic Product (GDP) per capita until a turning point around USD 3,000 per capita income, beyond which deforestation is expected to decline (Ajanaku and Collins, 2021). African apes are most threatened in areas with low to medium poverty, growing GDP, expanding agriculture, and growing rural populations (Tranquilli et al., 2012). Local economic development that spares forest or development away from forest areas could reduce population pressure and forest losses. The Sub-Saharan region is already undergoing rapid urbanization with forecasts indicating that ca. 58% of its population is going to live in cities by 2050 compared to ca. 40% now (UNDESA, 2019). Nevertheless, although overall annual growth rates have declined from 2.4% in 1980 to 1.7% in 2021 (The World Bank, 2022b), rural population growth is likely to continue. Resulting migration patterns in Sub-Saharan Africa are complex, even more so when driven by armed conflict (Mercandalli et al., 2019). While poverty levels may locally prevent deforestation, these may not be a good predictor of great ape survival itself. Ordaz-Németh et al. (2021) found a negative quadratic relationship between African great ape densities and GDP, with decreasing great ape densities, partially poaching-related, above a nationwide GDP of $5 billion annually, which translates into a per capita GDP for these countries between USD 500 and 2,500. The effects of GDP maybe therefore play out differently on deforestation and poaching, and poverty and income levels as such may be poor predictors of great ape survival.
The debate on land sharing versus land sparing is relevant to reducing negative interactions between people and great apes (Phalan et al., 2011; Law and Wilson, 2015). Land sparing aims to set aside large tracts of land for exclusive wildlife use while intensifying agriculture on existing farmland to keep people and great apes apart. Land sharing seeks coexistence between people and great apes through small-scale farming and sustainable forest management in patchworks of low-intensity agriculture. Empirical evaluations suggest that land sparing results in better outcomes for wildlife diversity and abundance in the short term (Phalan et al., 2011; Hulme et al., 2013; Williams et al., 2017), but others note that isolated protected areas within an agricultural matrix can increase inbreeding and vulnerability to extinction (Kremen and Merenlender, 2018). This has been demonstrated in orangutans (Bruford et al., 2010) and Cross-River gorillas (Bergl et al., 2008), although such effects will depend on the extent to which apes use the matrix. The impacts of intensive agriculture, such as the use of fertilizers, herbicides, fungicides, and pesticides (Matson and Vitousek, 2006; Dudley and Alexander, 2017), can also be harmful to great apes (Krief et al., 2017). Research suggests that intensification does not necessarily reduce the area under agriculture because high yields drive further agricultural expansion (Byerlee et al., 2014; Balmford, 2021). The reality for great apes is likely to remain a mixed sharing and sparing model, where parts of their remaining range will need to be included in protected areas while others will need to be shared with farmers (Meijaard et al., 2022b). Protected land is still necessary in these shared landscapes due to the low reproductive rates of great apes, their area requirements, and crop foraging. Therefore, land sparing-type solutions that safely protect habitat fragments and keep them connected are required for the synergistic coexistence of people and great apes (Ancrenaz et al., 2021).
4 Solutions for saving great apes in secure food systems
The coexistence of great apes and agriculture is challenging and a win-win situation for both is difficult to achieve. Agricultural expansion, often associated with people without prior experience of great ape coexistence moving into great ape areas, is likely to cause further declines in ape populations. This makes sustainable and resilient interactions between people and nature difficult to achieve. If we truly want to save great apes from extinction, then we must prioritize implementing strict spatial planning and rigorous enforcement measures, that are ideally co-developed with local communities. This includes designating no-farming areas, improving crop productivity and diversification, resolving human-wildlife conflicts, securing adequate conservation financing, and clearly defining the roles and responsibilities of different stakeholders (Table 3). Without a committed and sustained effort in these areas, the survival of great apes will remain uncertain, and the consequences of their extinction will be irreversible. Finding solutions that work for great apes would have implications for many other threatened species in similar socio-ecological contexts across the tropics.
Table 3 Primary food system archetypes for each great ape taxon based on country profiles by Marshall et al. (2021).
Great apes face competition for land and resources with humans, particularly where crops such as rice, cassava, maize, cacao, and oil palm are grown within their ranges (Table 3). This creates trade-offs between reducing poverty, feeding people, and conserving the environment. To address this, strategies must tackle the root causes of the problem, including land use competition. We suggest a framework for discussion, presented in Figure 5, focused on three directions. The first is to increase food production sustainably through agricultural innovations and smarter land use practices. The second is to modify food consumption patterns and distribution systems to reduce pressure on land and resources. Alternative food sources with minimal impact on great apes, including imported foods, might be effective under specific conditions. Though such lifestyle changes could raise complex issues related to food security and trade considerations. The third direction focuses on generating alternative income.
We emphasize the importance of adopting a landscape and jurisdictional approach in managing the competition between humans and great apes (Sayer et al., 2013). Within this framework, we propose several solutions, including strategies to increase yield, produce-and-protect practices, and threat management techniques. Next, we explore potential strategies to improve alternative income sources for communities, thereby reducing the need for land exploitation that can trigger competition with great apes (Figure 4). Finally, we consider the need to rethink our food systems in the context of the competition with great apes. We analyze potential solutions on both the consumption side and the production side, including modifying local food systems (e.g., by promoting dietary changes among local communities, such as switching from rice or maize to other crops) and global food systems (e.g., by reducing waste and rethinking food versus materials use) (Figure 5).
Figure 4 An adult male chimpanzee at Bossou in Guinea crossing a village homestead having foraged on a papaya fruit. Reprinted with permission from Kimberley Hockings (Cantanhez Chimpanzee Project).
Figure 5 Theory of Change and structure of Discussion.
4.1 Land use planning and landscape management
To resolve the great ape habitat-agricultural conflict, land use planning and implementation must consider crop impact on trade, consumption, and the environment. Plans should respect human rights and balance agricultural development with conservation in each priority area. They should assess crops and ecosystems, production scale and methods (Jansen et al., 2020). Smallholder agriculture, which dominates much of great ape habitat, can be challenging to regulate, and new financial models are needed to facilitate change among smallholders. An effective approach could focus on food systems rather than crops themselves (Marshall et al., 2021) (Figure 6) and the transformations these systems are undergoing (Dornelles et al., 2022). To diversify food systems, nutrient-rich legumes, pulses, horticulture crops, and livestock may be introduced. Investing in rural market infrastructure enables smallholders to commercialize and improve the availability of perishable products (Abraham and Pingali, 2020). Different food systems offer different transformation pathways, either in an agroecological direction based on the redesign and diversification of agroecosystems or following Fourth Industrial Revolution pathways characterized by new technologies (Pimbert, 2022).
Figure 6 Example of different primary food systems with great apes. (A) Rural and traditional; smallholder farm area in Sierra Leone near Gola Rainforest National Park. Google Earth image © 2023 Maxar Technologies and © 2023 CNES/Airbus; (B) Informal and expanding: farm area to the north of Bwindi Impenetrable Forest, Uganda Google Earth image © 2023 CNES/Airbus and © 2023 Maxar Technologies; (C) Emerging and diversifying; new oil palm development in Gabon in areas with chimpanzee and western gorilla populations. Google Earth image © Landsat/Copernicus; (D) Modernizing and formalizing: Lower Kinabatangan area in Sabah, Malaysia where 800 orangutans live in forest fragments surrounded by industrial-scale oil palm. Google Earth image © 2023 Maxar Technologies and © 2023 CNES/Airbus.
Government, farmers, industry, financial institutions, scientists, and civil society must collaborate for food system transformation. They should identify areas where the costs of agricultural conversion outweigh the benefits, considering environmental, social, and economic factors. Evaluating ecosystems’ economic, environmental, and social value before development is crucial. This includes assessing potential agricultural revenues and socio-political dynamics. Trade agreements and international finance are vital policy tools. Great apes play a key role in Performance Standard 6 of the International Finance Corporation, linking finance to conservation outcomes and avoiding negative impacts on apes. Priority great ape areas must be protected, and conservation organizations should engage stakeholders to establish “no-go” development zones based on factors such as food security and the importance of these areas for great ape populations (Ancrenaz et al., 2016). The World Bank and other financing entities adhere to these standards, allowing projects in great ape habitats only in exceptional circumstances.
Planning and implementation at the landscape scale is vital for great ape survival in human-dominated habitats. Orangutan populations are maintained in some oil palm concessions in Indonesia and Malaysia with selected areas of protected forest from a few hundred to several thousand hectares connected by forest corridors and riparian areas (Ancrenaz et al., 2015). Similarly, in Gabon, populations of chimpanzees and Western gorillas are maintained in areas of forest within an oil palm concession (Ancrenaz et al., 2016). Preliminary studies indicate that both orangutans and chimpanzees retain dispersal dynamics in fragmented landscapes that mirror those in large forests (i.e., female dispersal in chimpanzees and male dispersal in orangutans), as long as they are not hunted (McCarthy et al., 2018; Ancrenaz et al., 2021), and that the presence of corridors and small patches in the agricultural matrix likely increases population viability in orangutans (Seaman et al., 2021; Seaman et al., 2023).
4.1.1 Yield increases
Increasing productivity on existing agricultural lands can reduce the need for expansion (Zhang et al., 2021), but closing yield gaps for food security is challenging, potentially leading to more land expansion unless local demand is met by imports (van Ittersum et al., 2016). Boosting productivity through reduced fallow duration, multiple cropping, early-maturing varieties, intercropping, catch crops, and enhanced irrigation offers the largest potential for production increases (Poore and Nemecek, 2018). Furthermore, as productivity increases so do agricultural land rents, which could create new incentives for agricultural expansion and deforestation (Phelps et al., 2013). However, rising productivity in pre-established agricultural areas can attract local immigration away from vulnerable frontiers, promoting land sparing and nature conservation (Laurance et al., 2009; Laurance et al., 2015). Technological advances in established agricultural lands can help reduce deforestation if increased supply lowers market prices (Angelsen and Kaimowitz, 2001). This aligns with the Borlaug hypothesis – i.e., improvements in agricultural technology will enable farmers to produce more food from a given piece of land, thereby enabling growth in food supply without leading to increased deforestation – and the experience of the Green Revolution (Stevenson et al., 2013). Non-expansion and abandonment of marginal agricultural lands on the forest frontier are crucial for ‘forest transition’ processes, i.e., the stabilization or even increase of forest cover at high levels per-capita income (Mather and Needle, 1998; Meyfroidt and Lambin, 2011).
4.1.2 Produce-and-protect strategies
Another strategy could be to combine both policy tools – i.e., on the one hand land-use planning of ‘no-go’ conservation reserves on forest land with poor agricultural potential, and on the other improving agricultural yields on already cultivated land (Zhang et al., 2021). Such ‘produce-and-protect’ type of strategies of combining land-sparing agriculture with protected areas and private reserves for the provision of biodiversity services, indigenous lands and other actively enforced protection strategies may also be the most promising pathways for meeting the goals of great ape conservation and food production (Hanson and Ranganathan, 2022). Their attractive element is above all in their mutually reinforcing effects. On the one hand, effectively closing the agricultural frontier hampers land extensification and is inducive to the adoption of land-saving technologies that can increase producer incomes. Conversely, protecting land areas from crop expansion is easier when supply of the same crop is increasing and prices are not, thus counteracting any ‘leakage’ of forest pressures from the newly protected area to elsewhere (Meyfroidt et al., 2020).
Robust governance and increasing conservation incentives can help ensure land sparing, but implementation of these strategies may require tracking future agricultural land rents (Phelps et al., 2013) and targeting development planning away from core great ape areas (e.g., avoiding road building into or through priority habitats). This can stimulate economic growth and draw people away from frontier areas while increasing the value of natural ecosystems. Targeting development far from priority great ape areas makes sense as impacts on biodiversity are most severe in the earliest stages of agricultural expansion, especially when conversion occurs in forest interiors (Chaplin-Kramer et al., 2015). Conservation organizations should collaborate with governments and industry partners to build consensus about “no-go” areas for development based on the presence of priority great ape populations and other high-risk factors.
4.1.3 Food forests, regenerative agriculture and agroforestry
Improved agricultural methods are needed that reduce soil degradation and other negative environmental impacts and provide potential for climate solution (Terasaki Hart et al., 2023). This includes the increased use of agroforestry systems, which are thought to be more resilient than monocultures of annual crops (Mbow et al., 2014) and nitrogen-fixing legumes which increase soil fertility and reduce fertilizer needs and run-off (Roupsard et al., 2020). Agroforestry systems and perennial crops may also increase great ape dispersal between forest fragments as recorded in orangutans and chimpanzees. Mixing crops and forest patches does not necessarily reduce yields, because forests provide ecological benefits to surrounding agriculture that improves nearby yields, as demonstrated in Indonesian oil palm (Zemp et al., 2023). Many food forests are not yet economically viable but could be if other income could be generated from ecosystem services (Albrecht and Wiek, 2021).
4.1.4 Threat management and finance
Threat prevention strategies for great ape conservation require sustained external funding, which can come from various sources such as nature-based tourism (Maekawa et al., 2013) or funding from industry (Larson et al., 2021). Increased investment in patrolling and law enforcement, as well as the presence of civil society organizations, can help reduce pressure on great ape populations and habitats. To achieve this, there need to be new species action plans that call for a significant increase in and reallocation of conservation funding. Increasing the market value of biodiversity and allowing this to finance conservation services from nearby rural communities is one way to close the funding gap, while ensuring that funds end up where decisions about great apes are made (Ledgard and Meijaard, 2021; Fergus et al., 2023). The engagement of the private sector in conservation is another way to increase investment into biodiversity conservation, such as through offsetting biodiversity impacts or managing and maintaining species habitats (Bull and Strange, 2018). For example, palm oil certified through the Roundtable on Sustainable Palm Oil requires that areas of high conservation value are protected and values retained (RSPO, 2018). Effective management of great ape populations requires funding, manpower, and infrastructure which many companies have access to, but do not necessarily possess the knowledge to implement evidence-based conservation strategy. Furthermore, facilitating collaboration between industrial-scale operators and smallholders, such as has been attempted in the palm oil industry, can speed up knowledge transfer and increase yields for smallholders.
Increased funding is not enough. Efficient allocation of funds to more effective interventions is crucial. One billion USD allocated over 20 years to orangutan conservation was insufficient to stop their decline, probably due to inefficient allocation of funds (Santika et al., 2022). In summary, great ape conservation efforts require sustained external funding input and efficient allocation of funds to effective interventions. Increased investment in patrolling and law enforcement, preferably with the involvement of local communities, as well as the engagement of the private sector in conservation, can help achieve conservation goals. However, it is important to ensure that funds end up where ultimate decisions are made about great ape survival and that conservation efforts address not only habitat protection but also the safety of great apes from hunting, poaching, and disease. Evidence-based conservation is needed to investigate and determine what solutions will be most effective in different contexts local situations (Junker et al., 2020).
4.1.5 Key stakeholders and jurisdictional approach
Respecting human rights and effective engagement and motivation of communities living in proximity to great apes, in addition to earlier mentioned financial benefits, is essential for successful conservation (Chua et al., 2020; Bettinger et al., 2021). This needs to address the key question of what communities can gain from participating in conservation programs, and if they can help guide goals, planning and execution, i.e. “Whose Conservation” (see, e.g., Kaimowitz and Sheil, 2007; Mace, 2014). Engaging communities in conservation planning alongside broader village development planning could ensure that conservation objectives become integral to these broader plans (Vermeulen and Sheil, 2007; Meijaard et al., 2022b). Considerable experience exists in exploring, developing and implementing such initiatives (Lynam et al., 2007; Margules et al., 2020). The opportunities are generally greater than is assumed (Padmanaba and Sheil, 2007; Vermeulen and Sheil, 2007) as local people will often have goals and interests of their own that overlap with those of conservationists (Sheil et al., 2006; Chua et al., 2020). Working together to identify and achieve locally defined goals can be a useful means to build trust, reduce conflict and build a consensus towards addressing wider conservation goals (Sayer et al., 2013; Sheil et al., 2017). This could overcome the current problem that provisions for great ape conservation are often written by people who have little connection to or understanding of the livelihood strategies and patterns of indigenous communities (Chua et al., 2020).
4.2 Alternative income to avoid land competition with great apes
Achieving direct and immediate benefits for people who are asked to live side-by-side with great apes, for example through ecotourism (Robbins, 2021) or payments for conservation services (Ledgard and Meijaard, 2021; Fergus et al., 2023), could encourage more positive perceptions regarding apes that are becoming accustomed to human-dominated landscapes (Chua et al., 2020).
4.2.1 Eco-tourism
Eco-tourism provides a potential solution for achieving poverty eradication and conservation goals for communities facing imminent threats of agricultural expansion. The successful conservation of mountain gorillas has been largely funded by nature-based tourism (Maekawa et al., 2013), but this has also resulted in increased negative interactions between habituated gorillas and local communities (Hill, 2005; Seiler and Robbins, 2015; Robbins, 2021), highlighting the complexity of eco-tourism contexts. Nevertheless, the value of nature-based tourism to countries such as Rwanda is high with tourism accounting for 23%of export earnings in 2020 (World Bank and Government of Rwanda, 2020) and mountain gorillas alone accounting for 2% of GDP in 2023. In Borneo, eco-tourism businesses also contribute significantly to regional income (Goh and Potter, 2023), but scaling up tourism to cover the entire range of Bornean orangutan is challenging and may result in lower prices due to increased competition. While nature-based tourism can benefit great apes and local communities, it is unlikely to positively influence significant parts of the great apes’ range soon. The pandemic and the associated travel restrictions and periodic suspension of great ape visits have revealed the over-dependency on tourism (Ezra et al., 2021). Alternative financial mechanisms are needed to provide a safety net for communities when tourism does not bring in the much-needed resources.
4.2.2 Payment for biodiversity
Often the people who live with great apes see few economic benefits. As an example, around Bwindi Impenetrable Forest National Park, communities living within 0.5km of the boundaries are significantly poorer and are more affected by wild crop foraging animals than those living further away (Twinamatsiko et al., 2014). Conservation efforts, particularly the management of national parks, have historically exacerbated rural poverty by restricting access to forest resources, fining for minor acts and the loss of crops and livestock to protected wildlife (Blomley et al., 2010). Improved compensation schemes for conservation are therefore needed to finance the conservation of great apes and provide financial benefits to those living alongside them.
Developing payment for ecosystem services (PES) programs that financially incentivize local communities to conserve critical forested areas for great ape survival could be a potential approach (Wunder, 2005). To jumpstart financing for great ape conservation, compensation schemes for conservation could be combined with carbon credit schemes. To tackle this issue, a nested approach can be employed, incorporating carbon credits into a larger conservation project that encompasses biodiversity preservation and additional ecosystem services. (Law et al., 2012). The conservation project can generate carbon credits that can finance the broader conservation activities (but see West et al., 2023). The revenue generated can be used to compensate communities living with great apes or to restore degraded great ape habitat (Darusman et al., 2021). This approach can ensure that both biodiversity and carbon sequestration goals are achieved, and local communities benefit from conservation efforts.
One potential strategy is to establish fair and transparent compensation mechanisms to offset the costs that communities incur from living alongside great apes, such as damage to crops and livestock. Compensation programs can provide financial or material support to alleviate the economic losses inflicted by great apes, thus reducing conflicts between humans and wildlife and increasing the likelihood of coexisting with great apes in the long term. These programs can be supported by various sources, including conservation groups, government entities, and concerned private sector entities. Once such compensation schemes are established, they may need to remain in place indefinitely, and we acknowledge that running fair and transparent compensation schemes in many ape range countries would be a huge challenge.
Biocredits have emerged as an economic instrument to incentivize conservation in remote areas with great apes (Porras and Steele, 2020). Similar to carbon credits, they generate revenue by selling units of biodiversity resulting from improved conservation actions; how these units will be defined, measured and verified is yet unclear. Once this is resolved, biocredits can be purchased by government bodies, philanthropic organizations, and private companies. German companies have already expressed interest in purchasing biocredits for conservation through an online marketplace (Krause and Matzdorf, 2019). These mechanisms provide direct financial contributions to conservation organizations and communities, supporting initiatives like citizen science monitoring and tree planting. The use of biocredits for direct payments to individuals, communities, and local conservation managers is still limited but shows promise for the future (Community Conservation Namibia, 2023).
Interspecies Money is a proposed system designed to collect data on various species, provide them with a unique digital identity and digital wallets, and allocate based on the importance to conservation (Ledgard, 2022). Recent technological advancements, including low-cost sensors, drones, camera traps, bioacoustics, eDNA sampling, and artificial intelligence, enable data collection and analysis of population trends in their habitats (Ledgard and Kharas, 2022). This data-driven approach allows for the distribution of Interspecies Money based on conservation outcomes (increased abundance based on human behavior, e.g., a local farmer not cutting down a tree or not harming a great ape). This approach aims to simplify conservation finance, allowing easier upscaling and reducing the reliance on conservation organizations or governments. However, successful implementation requires redefining economic rules and piloting projects in natural settings to assess feasibility and effectiveness (Ledgard, 2022). The approach is being piloted in Rwanda.
4.3 Rethinking agriculture and food systems
4.3.1 Modifying global consumption and local agriculture
To address deforestation and protect great apes, requires understanding the consumption dynamics and underlying causes of agricultural expansion. Palm oil, for example, satisfies a significant portion of global vegetable oil demand (FAOSTAT, 2022), but reducing its use requires a shift in global consumption patterns (Goh, 2016; Meijaard and Sheil, 2019). Efforts to reduce reliance on palm oil must also consider potential adverse impacts on other regions and conservation efforts (Meijaard et al., 2020). Protecting great apes within the context of modern agriculture necessitates a comprehensive approach that considers the complex factors driving agricultural expansion, including internationally traded cash crops like cocoa, coffee, and oil palm. While a radical change in global consumption patterns solely for great ape protection is unlikely, efforts should be tied to larger issues such as climate change.
Promoting dietary changes within local communities can help reduce the demand for food production that destroys great ape habitats (Abraham and Pingali, 2020), as do reductions in food losses through improved storage and transportation. However, balancing conservation efforts with the food security of these communities presents a major challenge. Subsistence agriculture is vital for many people living in great ape regions, and altering their dietary choices and agricultural practices can have significant economic implications. Cultural and social barriers further complicate the process, requiring time and effort to implement changes. Education and capacity building programs can help transition local food systems to more sustainable practices. Such interventions must be approached with caution as they involve changing traditional ways of life.
4.3.2 Consumers’ awareness
There is an important role of consumers in putting pressure on retailers, producers and governments to ensure that the products they use are not associated with the loss of great apes and their habitats, or more generally, with the loss of biodiversity in tropical habitats. Currently, there is some consumer awareness about the environmental impacts of palm oil production on orangutans (e.g., Ostfeld et al., 2019), but much less so about, for example, chocolate consumption and chimpanzees. Providing consumers with fact-based and transparent information, e.g., through labelling processes, about the impact of the production rice, cassava, peanut, cacao and other crops in great apes’ ranges would give them a more informed choice and an ability to influence markets and land-use decision-making (Meijaard and Sheil, 2019). The European Union’s New Deforestation Regulation, although criticized by tropical producing countries such as Indonesia and Malaysia, provides a tool for consumers to differentiate products not on what they contain (e.g., a no-palm oil label) but rather as to how ingredients were produced (“great ape safe” or “deforestation free”). Also verified sustainable production practices such as those certified under the Roundtable on Sustainable Palm Oil can give consumers a more informed choice.
5 Conclusion
Great apes face significant threats from agriculture driven by poverty and demand for agricultural resources. Ensuring coexistence between great apes and people is of paramount importance, particularly considering that most great apes live outside protected areas. However, the challenge lies in the fact that on average each great ape shares its distribution range with approximately 100 people. Achieving successful coexistence requires significant incentives and efforts to protect and preserve these conservation flagships. New financial models are needed that can more easily be scaled up and attract =more investment. Optimized land use planning, guided by strategic investments in agricultural development and wildlife conservation, can maximize synergies between conservation and food production goals. It is vital to support effective economic development policies, enforce forest conservation and environmental laws, engage in trade policy discussions, and link policies on trade, food security, improved agricultural techniques, and sustainable food systems with forest and great ape impact monitoring. The global agenda should focus on closing crop yield gaps, promoting healthier diets, reducing food loss and waste, and allocating more research funding to address the challenges of great ape and human coexistence.
Author contributions
EM, RD, MA, SWi and DS contributed to conception and design of the study. NU, TA and RD organized the database and spatial analysis of crop and other data. JS developed the causal change diagrams. EM wrote the first draft of the manuscript. KH, SWu, CG, MO, JL, JR, and DS wrote sections of the manuscript. All authors contributed to manuscript revision, read, and approved the submitted version.
Funding
Work was supported via a grant from UNEP GRASP (SSFA/2021/4079) and a grant from UNEP under the GEF funded Congo Basin Impact Program (PCA/2022/5067) and the Darwin Initiative (grant number, 26-018) to KH.
Conflict of interest
EM, NU, TA, RD and MA were employed by Borneo Futures.
EM declares that he co-chairs the IUCN Oil Crops Task Force that studies oil crops. He has received funding from palm oil producing companies and the Roundtable on Sustainable Palm Oil, which could be construed as a potential conflict of interest.
The remaining authors declare that the research was conducted in the absence of any commercial or financial relationships that could be construed as a potential conflict of interest.
Publisher’s note
All claims expressed in this article are solely those of the authors and do not necessarily represent those of their affiliated organizations, or those of the publisher, the editors and the reviewers. Any product that may be evaluated in this article, or claim that may be made by its manufacturer, is not guaranteed or endorsed by the publisher.
Supplementary material
The Supplementary Material for this article can be found online at: https://www.frontiersin.org/articles/10.3389/fcosc.2023.1225911/full#supplementary-material
References
Abraham M., Pingali P. (2020). “Transforming smallholder agriculture to achieve the SDGs,” in The Role of Smallholder Farms in Food and Nutrition Security. Eds. Paloma S.G. Y., Riesgo L., Louhichi K. (Cham, Switzerland: Springer), 173–191.
Ajanaku B. A., Collins A. R. (2021). Economic growth and deforestation in African countries: Is the environmental Kuznets curve hypothesis applicable? For. Policy Economics 129, 102488. doi: 10.1016/j.forpol.2021.102488
Akpabio E. M. (2007). Assessing integrated water resources management in Nigeria: insights and lessons from irrigation projects in the Cross River Basin. Water Policy 9, 149–168. doi: 10.2166/wp.2007.007
Albrecht S., Wiek A. (2021). Food forests: Their services and sustainability. J. Agriculture Food Systems Community Dev. 10, 91–105. doi: 10.5304/jafscd.2021.103.014
Ancrenaz M., Meijaard E., Wich S. A., Simery J. (2016). Palm oil paradox. Sustainable solutions to save the great apes. (Nairobi, Kenya: UNEP/GRASP).
Ancrenaz M., Oram F., Ambu L., Lackman I., Ahmad E., Elahan H., et al. (2015). Of pongo, palms, and perceptions – A multidisciplinary assessment of orangutans in an oil palm context. Oryx 49, 465–472. doi: 10.1017/S0030605313001270
Ancrenaz M., Oram F., Nardiyono, Silmi M., Jopony M. E. M., Voigt M., et al. (2021). Importance of orangutans in small fragments for maintaining metapopulation dynamics. Front. Forests Global Change 4, 560944.
Angelsen A., Kaimowitz D. (2001). Agricultural technologies and tropical deforestation. (Bogor, Indonesia: CIFOR).
Antony Ceasar S., Maharajan T. (2022). The role of millets in attaining United Nation’s sustainable developmental goals. PLANTS PEOPLE PLANET 4, 345–349. doi: 10.1002/ppp3.10254
Balmford A. (2021). Concentrating vs. spreading our footprint: how to meet humanity’s needs at least cost to nature. J. Zoology 315, 79–109. doi: 10.1111/jzo.12920
Bergl R. A., Bradley B. J., Nsubuga A., Vigilant L. (2008). Effects of habitat fragmentation, population size and demographic history on genetic diversity: the cross river gorilla in a comparative context. Am. J. Primatology 70, 848–859. doi: 10.1002/ajp.20559
Bersacola E., Hill C. M., Hockings K. J. (2021). Chimpanzees balance resources and risk in an anthropogenic landscape of fear. Sci. Rep. 11, 4569. doi: 10.1038/s41598-021-83852-3
Bettinger T., Cox D., Kuhar C., Leighty K. (2021). Human engagement and great ape conservation in Africa. Am. J. Primatology 83, e23216. doi: 10.1002/ajp.23216
Blomley T., Namara A., McNeilage A., Franks P., Rainer H., Donaldson A., et al. (2010). Development AND Gorillas? Assessing fifteen years of integrated conservation and development in south-western Uganda (London, UK: Natural Resource Issues (23). IIED).
Brncic T., Amarasekaran B., McKenna A., Mundry R., Kühl H. S. (2015). Large mammal diversity and their conservation in the human-dominated land-use mosaic of Sierra Leone. Biodiversity Conserv. 24, 2417–2438. doi: 10.1007/s10531-015-0931-7
Bruford M. W., Ancrenaz M., Chikhi L., Lackman-Ancrenaz I., Andau M., Ambu L., et al. (2010). Projecting genetic diversity and population viability for the fragmented orang-utan population in the Kinabatangan floodplain, Sabah, Malaysia. Endangered Species Res. 12, 249–261. doi: 10.3354/esr00295
Bull J. W., Strange N. (2018). The global extent of biodiversity offset implementation under no net loss policies. Nat. Sustainability 1, 790–798. doi: 10.1038/s41893-018-0176-z
Busch J., Ferretti-Gallon K. (2017). What drives deforestation and what stops it? A meta-analysis. Rev. Environ. Economics Policy 11, 3–23. doi: 10.1093/reep/rew013
Byerlee D., Stevenson J., Villoria N. (2014). Does intensification slow crop land expansion or encourage deforestation? Global Food Secur. 3, 92–98. doi: 10.1016/j.gfs.2014.04.001
Caldecott J., Miles L. (2006). World Atlas of Great Apes and their Conservation (Cambridge, UK: UNEP World Conservation Monitoring Centre).
Campbell-Smith G., Campbell-Smith M., Singleton I., Linkie M. (2011). Raiders of the lost bark: orangutan foraging strategies in a degraded landscape. PloSONE 6, e20962. doi: 10.1371/journal.pone.0020962
Campbell-Smith G., Sembiring R., Linkie M. (2012). Evaluating the effectiveness of human-orangutan conflict mitigation strategies in Sumatra. J. Appl. Ecol. 49, 367–375. doi: 10.1111/j.1365-2664.2012.02109.x
Carter N. H., Linnell J. D. C. (2016). Co-adaptation is key to coexisting with large carnivores. Trends Ecol. Evol. 31, 575–578. doi: 10.1016/j.tree.2016.05.006
Chaplin-Kramer R., Sharp R. P., Mandle L., Sim S., Johnson J., Butnar I., et al. (2015). Spatial patterns of agricultural expansion determine impacts on biodiversity and carbon storage. Proc. Natl. Acad. Sci. 112, 7402–7407. doi: 10.1073/pnas.1406485112
Chua L., Harrison M., Cheyne S., Fair H., Milne S., Palmer A., et al. (2020). Conservation and the social sciences: beyond critique and co-optation. A case study from orangutan conservation. People Nat. 2, 42–60. doi: 10.1002/pan3.10072
Cincotta R. P., Wisnewski J., Engelman R. (2000). Human population in the biodiversity hotspots. Nature 404, 990–992. doi: 10.1038/35010105
Community Conservation Namibia (2023) Wildlife Credits, an incentive to conserve. Available at: https://wildlifecredits.com/how-we-work (Accessed 15 May 2023).
Darusman T., Lestari D. P., Arriyadi D. (2021). “Management practice and restoration of the peat swamp forest in Katingan-Mentaya, Indonesia,” in Tropical Peatland Eco-management. Eds. Osaki M., Tsuji N., Foead N., Rieley J. (Singapore: Springer Singapore), 381–409.
Dornelles A. Z., Boonstra W. J., Delabre I., Denney J. M., Nunes R. J., Jentsch A., et al. (2022). Transformation archetypes in global food systems. Sustainability Sci. 17, 1827–1840. doi: 10.1007/s11625-022-01102-5
Dudley N., Alexander S. (2017). Agriculture and biodiversity: a review. Biodiversity 18, 45–49. doi: 10.1080/14888386.2017.1351892
Duffy C., Toth G. G., Hagan R. P. O., McKeown P. C., Rahman S. A., Widyaningsih Y., et al. (2021). Agroforestry contributions to smallholder farmer food security in Indonesia. Agroforestry Syst. 95, 1109–1124. doi: 10.1007/s10457-021-00632-8
Ekpa O., Palacios-Rojas N., Kruseman G., Fogliano V., Linnemann A. R. (2019). Sub-saharan african maize-based foods - processing practices, challenges and opportunities. Food Rev. Int. 35, 609–639. doi: 10.1080/87559129.2019.1588290
Erenstein O., Jaleta M., Sonder K., Mottaleb K., Prasanna B. M. (2022). Global maize production, consumption and trade: trends and R&D implications. Food Security. 14, 1295–1319. doi: 10.1007/s12571-022-01288-7
Ezra P., Kitheka B., Sabuhoro E., Riungu G., Sirima A., Amani A., et al. (2021). Responses and impacts of COVID-19 on east Africa’s tourism industry. Afr. J. Hospitality Tourism Leisure 10, 1711–1727. doi: 10.46222/ajhtl.19770720.188
Fahy G. E., Richards M., Riedel J., Hublin J.-J., Boesch C. (2013). Stable isotope evidence of meat eating and hunting specialization in adult male chimpanzees. Proc. Natl. Acad. Sci. 110, 5829–5833. doi: 10.1073/pnas.1221991110
FAOSTAT (2022). Food and agriculture data (Rome, Italy: The Food and Agriculture Organization (FAO).
FAOSTAT (2023). Crops and livestock products (Rome, Italy: Food and Agriculture Organization of the United Nations). Available at: https://www.fao.org/faostat/en/#data/QCL.
Fergus P., Chalmers C., Longmore S., Wich S., Warmenhove C., Swart J., et al. (2023). Empowering wildlife guardians: an equitable digital stewardship and reward system for biodiversity conservation using deep learning and 3/4G camera traps. Remote Sens. 15, 2730. doi: 10.3390/rs15112730
Fletcher S. M., Shi Z. (2016). “Chapter 10 - an overview of world peanut markets,” in Peanuts. Eds. Stalker H. T., Wilson R. F. (Cambridge, MA, USA: AOCS Press), 267–287.
Garcia C. A., Savilaakso S., Verburg R. W., Gutierrez V., Wilson S. J., Krug C. B., et al. (2020). The global forest transition as a human affair. One Earth 2, 417–428. doi: 10.1016/j.oneear.2020.05.002
Garriga R. M., Marco I., Casas-Díaz E., Amarasekaran B., Humle T. (2018). Perceptions of challenges to subsistence agriculture, and crop foraging by wildlife and chimpanzees Pan troglodytes verus in unprotected areas in Sierra Leone. Oryx 52, 761–774. doi: 10.1017/S0030605316001319
Gaveau D. L. A., Locatelli B., Descals A., Manurung T., Salim M. A., Husnayen, et al. (2022). Slowing oil palm expansion and deforestation in Indonesia coincide with low oil prices. PloS One 17, e0266178. doi: 10.1371/journal.pone.0266178
Gaveau D. L. A., Locatelli B., Salim M. A., Yaen H., Pacheco P., Sheil D. (2019). Rise and fall of forest loss and industrial plantations in Borneo, (2000–2017). Conserv. Lett. 12, e12622. doi: 10.1111/conl.12622
Giller K. E. (2020). The food security conundrum of sub-saharan Africa. Global Food Secur. 26, 100431. doi: 10.1016/j.gfs.2020.100431
Goh C. S. (2016). Can we get rid of palm oil? Trends Biotechnol. 34, 948–950. doi: 10.1016/j.tibtech.2016.08.007
Goh C. S., Potter L. (2023). Transforming Borneo: From Land Exploitation to Sustainable Development (Singapore: ISEAS–Yusof Ishak Institute Singapore).
Grant M. J., Booth A. (2009). A typology of reviews: an analysis of 14 review types and associated methodologies. Health Inf. Libraries J. 26, 91–108. doi: 10.1111/j.1471-1842.2009.00848.x
Halloran A. R. (2016). “The many facets of human disturbances at the tonkolili chimpanzee site,” in Ethnoprimatology: Primate Conservation in the 21st Century. Ed. Waller M. T. (Cham: Springer International Publishing), 273–281.
Halpern B. S., Frazier M., Verstaen J., Rayner P.-E., Clawson G., Blanchard J. L., et al. (2022). The environmental footprint of global food production. Nat. Sustainability 5, 1027–1039. doi: 10.1038/s41893-022-00965-x
Hanson C., Ranganathan J. (2022). How to Manage the Global Land Squeeze? Produce, Protect, Reduce, Restore (Washington DC: World Resources Institute (WRI).
Harihar A., Chanchani P., Sharma R. K., Vattakaven J., Gubbi S., Pandav B., et al. (2013). Conflating “co-occurrence” with “coexistence”. Proc. Natl. Acad. Sci. 110, E109–E109. doi: 10.1073/pnas.1217001110
Heinicke S., Mundry R., Boesch C., Amarasekaran B., Barrie A., Brncic T., et al. (2019). Characteristics of positive deviants in western chimpanzee populations. Front. Ecol. Evol. 7. doi: 10.3389/fevo.2019.00016
Hengl T., Miller M. A. E., Križan J., Shepherd K. D., Sila A., Kilibarda M., et al. (2021). African soil properties and nutrients mapped at 30 m spatial resolution using two-scale ensemble machine learning. Sci. Rep. 11, 6130. doi: 10.1038/s41598-021-85639-y
Hill C. M. (2005). “People, crops and primates: a conflict of interests,” in Primate commensalism and conflict. Eds. Paterson J. D., Wallis J.. (American Society of Primatologists). 41–59.
Hill C. M. (2017). Primate crop feeding behavior, crop protection, and conservation. Int. J. Primatology 38, 385–400. doi: 10.1007/s10764-017-9951-3
Hockings K. J., Anderson J. R., Matsuzawa T. (2009). Use of wild and cultivated foods by chimpanzees at Bossou, Republic of Guinea: feeding dynamics in a human-influenced environment. Am. J. Primatology 71, 636–646. doi: 10.1002/ajp.20698
Hockings K., Humle T. (2009). Best Practice Guidelines for the Prevention and Mitigation of Conflict Between Humans and Great Apes (Gland, Switzerland: IUCN SSC Primate Specialist Group).
Hockings K. J., McLennan M. R. (2012). From forest to farm: systematic review of cultivar feeding by chimpanzees – management implications for wildlife in anthropogenic landscapes. PloS One 7, e33391. doi: 10.1371/journal.pone.0033391
Hockings K. J., McLennan M. R., Carvalho S., Ancrenaz M., Bobe R., Byrne R. W., et al. (2015). Apes in the Anthropocene: flexibility and survival. Trends Ecol. Evol. 30, 215–222. doi: 10.1016/j.tree.2015.02.002
Hulme M. F., Vickery J. A., Green R. E., Phalan B., Chamberlain D. E., Pomeroy D. E., et al. (2013). Conserving the birds of Uganda’s banana-coffee arc: land sparing and land sharing compared. PloS One 8, e54597. doi: 10.1371/journal.pone.0054597
Independent Science and Parnership Council (2016). Agricultural Growth Corridors. Mapping potential research gaps on impact, implementation and institutions (Nairobi, Kenya: CGIAR, Independent Science and Parnership Council and European Centre for Development Policy Management).
Jansen M., Guariguata M. R., Raneri J. E., Ickowitz A., Chiriboga-Arroyo F., Quaedvlieg J., et al. (2020). Food for thought: The underutilized potential of tropical tree-sourced foods for 21st century sustainable food systems. People Nat. 2, 1006–1020. doi: 10.1002/pan3.10159
Jayathilake H. M., Prescott G. W., Carrasco L. R., Rao M., Symes W. S. (2021). Drivers of deforestation and degradation for 28 tropical conservation landscapes. Ambio 50, 215–228. doi: 10.1007/s13280-020-01325-9
Junker J., Petrovan S. O., Arroyo-RodrÍguez V., Boonratana R., Byler D., Chapman C. A., et al. (2020). A severe lack of evidence limits effective conservation of the world’s primates. BioScience 70, 794–803. doi: 10.1093/biosci/biaa082
Kaimowitz D., Sheil D. (2007). Conserving what and for whom? Why conservation should help meet basic human needs in the tropics. Biotropica 39, 567–574. doi: 10.1111/j.1744-7429.2007.00332.x
Kalan A. K., Kulik L., Arandjelovic M., Boesch C., Haas F., Dieguez P., et al. (2020). Environmental variability supports chimpanzee behavioral diversity. Nat. Commun. 11, 4451. doi: 10.1038/s41467-020-18176-3
Kormos R., Boesch C., Bakarr M. I., Butynski T. M. (2003). West African Chimpanzees: Status, Survey and Conservation Action Plan (Gland, Switzerland: International Union for Conservation of Nature (IUCN) World Conservation Union).
Kottek M., Grieser J., Beck C., Rudolf B., Rubel F. (2006). World Map of the Köppen-Geiger climate classification updated. Meteorologische Z. 15, 259–263. doi: 10.1127/0941-2948/2006/0130
Krause M. S., Matzdorf B. (2019). The intention of companies to invest in biodiversity and ecosystem services credits through an online-marketplace. Ecosystem Serv. 40, 101026. doi: 10.1016/j.ecoser.2019.101026
Kremen C., Merenlender A. M. (2018). Landscapes that work for biodiversity and people. Science 362, eaau6020. doi: 10.1126/science.aau6020
Krief S., Berny P., Gumisiriza F., Gross R., Demeneix B., Fini J. B., et al. (2017). Agricultural expansion as risk to endangered wildlife: Pesticide exposure in wild chimpanzees and baboons displaying facial dysplasia. Sci. Total Environ. 598, 647–656. doi: 10.1016/j.scitotenv.2017.04.113
Kumar A., Tomer V., Kaur A., Kumar V., Gupta K. (2018). Millets: a solution to agrarian and nutritional challenges. Agric. Food Secur. 7, 31. doi: 10.1186/s40066-018-0183-3
Larson L. R., Peterson M. N., Furstenberg R. V., Vayer V. R., Lee K. J., Choi D. Y., et al. (2021). The future of wildlife conservation funding: What options do U.S. college students support? Conserv. Sci. Pract. 3, e505. doi: 10.1111/csp2.505
Laso Bayas J. C., See L., Georgieva I., Schepaschenko D., Danylo O., Dürauer M., et al. (2022). Drivers of tropical forest loss between 2008 and 2019. Sci. Data 9, 146. doi: 10.1038/s41597-022-01227-3
Laurance W. F., Goosem M., Laurance S. G. (2009). Impacts of roads and linear clearings on tropical forests. Trends Ecol. Evol. 24, 659–669. doi: 10.1016/j.tree.2009.06.009
Laurance W. F., Sloan S., Weng L., Sayer J. A. (2015). Estimating the environmental costs of Africa’s massive “Development corridors”. Curr. Biol. 25, 3202–3208. doi: 10.1016/j.cub.2015.10.046
Law E. A., Thomas S., Meijaard E., Dargusch P. J., Wilson K. A. (2012). A modular framework for management of complexity in international forest-carbon policy. Nat. Climate Change 2, 155–160. doi: 10.1038/nclimate1376
Law E. A., Wilson K. A. (2015). Providing context for the land-sharing and land-sparing debate. Conserv. Lett. 8, 404–413. doi: 10.1111/conl.12168
Ledgard J. (2022). “Interspecies money,” in Breakthrough: The Promise of Frontier Technologies for Sustainable Development. Eds. Kharas H., Mcarthur J. W., Ohno I. (Washington, D.C: Brookings Institution Press), 77–102.
Ledgard J., Kharas H. (2022) Financing the preservation of diverse life on Earth in a capitalist system. Available at: https://www.brookings.edu/blog/future-development/2022/02/15/financing-the-preservation-of-diverse-life-on-earth-in-a-capitalist-system/ (Accessed 15 May 2023).
Ledgard J., Meijaard E. (2021). Endangered wildlife should pay for its own protection. (Project Syndicate). Available at: https://www.project-syndicate.org/commentary/digital-wallets-for-endangered-wild-animals-by-jonathan-ledgard-1-and-erik-meijaard-2021-2012.
Lesiv M., Laso Bayas J. C., See L., Duerauer M., Dahlia D., Durando N., et al. (2019). Estimating the global distribution of field size using crowdsourcing. Global Change Biol. 25, 174–186. doi: 10.1111/gcb.14492
Linder J. M. (2013). African primate diversity threatened by “New wave” of industrial oil palm expansion. Afr. Primates 8, 25–38.
Lynam T., De Jong W., Sheil D., Kusumanto T., Evans K. (2007). A review of tools for incorporating community knowledge, preferences, and values into decision making in natural resources management. Ecol. Soc. 12. doi: 10.5751/ES-01987-120105
Maekawa M., Lanjouw A., Rutagarama E., Sharp D. (2013). Mountain gorilla tourism generating wealth and peace in post-conflict Rwanda. Natural Resour. Forum 37, 127–137. doi: 10.1111/1477-8947.12020
Margules C., Boedhihartono A. K., Langston J. D., Riggs R. A., Sari D. A., Sarkar S., et al. (2020). Transdisciplinary science for improved conservation outcomes. Environ. Conserv. 47, 224–233. doi: 10.1017/S0376892920000338
Marshall Q., Fanzo J., Barrett C. B., Jones A. D., Herforth A., McLaren R. (2021). Building a global food systems typology: A new tool for reducing complexity in food systems analysis. Front. Sustain. Food Syst. 5. doi: 10.3389/fsufs.2021.746512
Masi S., Chauffour S., Bain O., Todd A., Guillot J., Krief S. (2012). Seasonal effects on great ape health: A case study of wild chimpanzees and western gorillas. PloS One 7, e49805. doi: 10.1371/journal.pone.0049805
Mather A. S., Needle C. L. (1998). The forest transition: a theoretical basis. Area 30, 117–124. doi: 10.1111/j.1475-4762.1998.tb00055.x
Matson P. A., Vitousek P. M. (2006). Agricultural intensification: will land spared from farming be land spared for nature? Conserv. Biol. 20, 709–710. doi: 10.1111/j.1523-1739.2006.00442.x
Mbow C., Van Noordwijk M., Luedeling E., Neufeldt H., Minang P. A., Kowero G. (2014). Agroforestry solutions to address food security and climate change challenges in Africa. Curr. Opin. Environ. Sustainability 6, 61–67. doi: 10.1016/j.cosust.2013.10.014
McAlpine C. A., Johnson A., Salazar A., Syktus J., Wilson K., Meijaard E., et al. (2018). Forest loss and Borneo’s climate. Environ. Res. Lett. 13, 044009. doi: 10.1088/1748-9326/aaa4ff
McCarthy M. S., Lester J. D., Langergraber K. E., Stanford C. B., Vigilant L. (2018). Genetic analysis suggests dispersal among chimpanzees in a fragmented forest landscape in Uganda. Am. J. Primatology 80, e22902. doi: 10.1002/ajp.22902
McLennan M. R. (2013). Diet and Feeding Ecology of Chimpanzees (Pan troglodytes) in Bulindi, Uganda: Foraging Strategies at the Forest–Farm Interface. Int. J. Primatology 34, 585–614. doi: 10.1007/s10764-013-9683-y
McLennan M. R., Hintz B., Kiiza V., Rohen J., Lorenti G. A., Hockings K. J. (2021). Surviving at the extreme: Chimpanzee ranging is not restricted in a deforested human-dominated landscape in Uganda. Afr. J. Ecol. 59, 17–28. doi: 10.1111/aje.12803
McLennan M. R., Hockings K. J. (2014). Wild chimpanzees show group differences in selection of agricultural crops. Sci. Rep. 4, 5956. doi: 10.1038/srep05956
Meijaard E. (2017). “How a mistaken ecological narrative could be undermining orangutan conservation,” in Effective Conservation Science: Data Not Dogma. Eds. Kareiva P., Marvier M., Silliman B. (Oxford, UK: Oxford University Press), 90–97.
Meijaard E., Abrams J. F., Slavin J. L., Sheil D. (2022a). Dietary fats, human nutrition and the environment: balance and sustainability. Front. Nutr. 9. doi: 10.3389/fnut.2022.878644
Meijaard E., Ariffin T., Unus N., Dennis R., Wich S. A., Ancrenaz M. (2021). Great apes and oil palm in a broader agricultural context. Report by Borneo Futures and the IUCN Oil Crops Task Force for UNEP/GRASP (Bandar Seri Begawan, Brunei Darussalam: Borneo Futures and the IUCN Oil Crops Task Force).
Meijaard E., Brooks T. M., Carlson K. M., Slade E. M., Garcia-Ulloa J., Gaveau D. L. A., et al. (2020). The environmental impacts of palm oil in context. Nat. Plants 6, 1418–1426. doi: 10.1038/s41477-020-00813-w
Meijaard E., Sheil D. (2019). The moral minefield of ethical oil palm and sustainable development. Front. Forests Global Change 2. doi: 10.3389/ffgc.2019.00022
Meijaard E., Sheil D., Sherman J., Chua L., Ni’matullah S., Wilson K., et al. (2022b). Restoring the orangutan in a Whole- or Half-Earth context. Oryx 566–577. doi: 10.1017/S003060532200093X
Meijaard E., Welsh A., Ancrenaz M., Wich S., Nijman V., Marshall A. J. (2010). Declining orangutan encounter rates from Wallace to the present suggest the species was once more abundant. PlosONE 5, e12042. doi: 10.1371/journal.pone.0012042
Mercandalli S., Losch B., Belebema M. N., Bélières J.-F., Bourgeois R., Dinbabo M. F., et al. (2019). Rural migration in sub–Saharan Africa: Patterns, drivers and relation to structural transformation (Rome, Italy: FAO and CIRAD).
Meyfroidt P., Börner J., Garrett R., Gardner T., Godar J., Kis-Katos K., et al. (2020). Focus on leakage and spillovers: informing land-use governance in a tele-coupled world. Environ. Res. Lett. 15, 090202. doi: 10.1088/1748-9326/ab7397
Meyfroidt P., Lambin E. F. (2011). Global forest transition: prospects for an end to deforestation. Annu. Rev. Environ. Resour. 36, 343–371. doi: 10.1146/annurev-environ-090710-143732
Mukasa A. N., Woldemichael A. D., Salami A. O., Simpasa A. M. (2017). Africa’s agricultural transformation: identifying priority areas and overcoming challenges. Afr. Economic Brief 8, 1–16.
Mundia C. W., Secchi S., Akamani K., Wang G. (2019). A regional comparison of factors affecting global sorghum production: the case of North America, Asia and Africa’s Sahel. Sustainability 11, 2135. doi: 10.3390/su11072135
Muthayya S., Sugimoto J. D., Montgomery S., Maberly G. F. (2014). An overview of global rice production, supply, trade, and consumption. Ann. New York Acad. Sci. 1324, 7–14. doi: 10.1111/nyas.12540
Naughton-Treves L., Treves A., Chapman C. A., Wrangham R. W. (1998). Temporal patterns of crop-raiding by primates: linking food availability in croplands and adjacent forest. J. Appl. Ecol. 35, 596–606. doi: 10.1046/j.1365-2664.1998.3540596.x
Oram F., Kapar M. D., Saharon A. R., Elahan H., Segaran P., Poloi S., et al. (2022). “Engaging the Enemy”: Orangutan (Pongo pygmaeus morio) Conservation in Human Modified Environments in the Kinabatangan floodplain of Sabah, Malaysian Borneo. Int. J. Primatol 43, 1–28. doi: 10.1007/s10764-022-00288-w
Ordaz-Németh I., Sop T., Amarasekaran B., Bachmann M., Boesch C., Brncic T., et al. (2021). Range-wide indicators of African great ape density distribution. Am. J. Primatology 83, e23338. doi: 10.1002/ajp.23338
Ostfeld R., Howarth D., Reiner D., Krasny P. (2019). Peeling back the label—exploring sustainable palm oil ecolabelling and consumption in the United Kingdom. Environ. Res. Lett. 14, 014001. doi: 10.1088/1748-9326/aaf0e4
Padmanaba M., Sheil D. (2007). Finding and promoting a local conservation consensusin a globally important tropical forest landscape. Biodiversity Conserv. 16, 137–151. doi: 10.1007/s10531-006-9009-x
Pendrill F., Gardner T. A., Meyfroidt P., Persson U. M., Adams J., Azevedo T., et al. (2022). Disentangling the numbers behind agriculture-driven tropical deforestation. Science 377, eabm9267. doi: 10.1126/science.abm9267
Péter H., Zuberbühler K., Hobaiter C. (2022). Well-digging in a community of forest-living wild East African chimpanzees (Pan troglodytes schweinfurthii). Primates 63, 355–364. doi: 10.1007/s10329-022-00992-4
Phalan B., Onial M., Balmford A., Green R. E. (2011). Reconciling food production and biodiversity conservation: land sharing and land sparing compared. Science 333, 1289–1291. doi: 10.1126/science.1208742
Phelps J., Carrasco L. R., Webb E. L., Koh L. P., Pascual U. (2013). Agricultural intensification escalates future conservation costs. Proc. Natl. Acad. Sci. 110, 7601–7606. doi: 10.1073/pnas.1220070110
Pimbert M. P. (2022). Transforming food and agriculture: Competing visions and major controversies. Mondes en développement 199-200, 361–384. doi: 10.3917/med.199.0365
Poore J., Nemecek T. (2018). Reducing food’s environmental impacts through producers and consumers. Science 360, 987–992. doi: 10.1126/science.aaq0216
Porras I., Steele P. (2020). Biocredits. A solution for protecting nature and tackling poverty Environmental Economics. Issue Paper February 2020 (London: IIED).
Potapov P., Turubanova S., Hansen M. C., Tyukavina A., Zalles V., Khan A., et al. (2022). Global maps of cropland extent and change show accelerated cropland expansion in the twenty-first century. Nat. Food 3, 19–28. doi: 10.1038/s43016-021-00429-z
Rainer H., White A., Lanjouw A. (2020). State of the Apes. Killing, Capture, Trade and Conservation (Cambridge, UK: Cambridge University Press).
Rakotoarisoa M. A., Lafrate M., Paschali M. (2012). Why has Africa become a Net Food Importer? Explaining Africa Agricultural and Food Trade Deficits (Rome, Italy: Food and Agriculture Organization).
Ranum P., Peña-Rosas J. P., Garcia-Casal M. N. (2014). Global maize production, utilization, and consumption. Ann. New York Acad. Sci. 1312, 105–112. doi: 10.1111/nyas.12396
Robbins M. M. (2021). Assessing attitudes towards gorilla conservation via employee interviews. Am. J. Primatology 83, e23191. doi: 10.1002/ajp.23191
Roupsard O., Audebert A., Ndour A. P., Clermont-Dauphin C., Agbohessou Y., Sanou J., et al. (2020). How far does the tree affect the crop in agroforestry? New spatial analysis methods in a Faidherbia parkland. Agriculture Ecosyst. Environ. 296, 106928. doi: 10.1016/j.agee.2020.106928
RSPO (2018). RSPO Principles & Criteria Certification For the Production of Sustainable Palm Oil. 2018 (Kualu Lumpur, Malaysia: Roundtable on Sustainable Palm Oil).
Sanchez P. A. (2002). Soil fertility and hunger in Africa. Science 295, 2019–2020. doi: 10.1126/science.1065256
Sandker M., Campbell B. M., Nzooh Z., Sunderland T., Amougou V., Defo L., et al. (2009). Exploring the effectiveness of integrated conservation and development interventions in a Central African forest landscape. Biodiversity Conserv. 18, 2875–2892. doi: 10.1007/s10531-009-9613-7
Santika T., Sherman J., Voigt M., Ancrenaz M., Wich S. A., Wilson K. A., et al. (2022). Effectiveness of 20 years of conservation investments in protecting orangutans. Curr. Biol. 32, 1754–1763.e1756. doi: 10.1016/j.cub.2022.02.051
Santika T., Wilson K. A., Budiharta S., Kusworo A., Meijaard E., Law E. A., et al. (2019). Heterogeneous impacts of community forestry on forest conservation and poverty alleviation: Evidence from Indonesia. People Nat. 1, 204–219. doi: 10.1002/pan3.25
Sayer J., Sunderland T., Ghazoul J., Pfund J.-L., Sheil D., Meijaard E., et al. (2013). Ten principles for a landscape approach to reconciling agriculture, conservation, and other competing land uses. Proc. Natl. Acad. Sci. United States America 110, 8349–8356. doi: 10.1073/pnas.1210595110
Schiavina M., Freire S., MacManus K. (2022). GHS-POP R2022A - GHS population grid multitemporal, (1975-2030) (Ispra, Italy: European Commission, Joint Research Centre (JRC). Available at: http://data.europa.eu/89h/d6d86a90-4351-4508-99c1-cb074b022c4a.
Schmitz C., van Meijl H., Kyle P., Nelson G. C., Fujimori S., Gurgel A., et al. (2014). Land-use change trajectories up to 2050: insights from a global agro-economic model comparison. Agric. Economics 45, 69–84. doi: 10.1111/agec.12090
Seaman D. J. I., Voigt M., Ancrenaz M., Bocedi G., Meijaard E., Oram F., et al. (2023). Capacity for recovery in Bornean orangutan populations if forest fragmentation and offtake is limited. (Authorea). doi: 10.22541/au.169382404.49701088/v1
Seaman D. J. I., Voigt M., Bocedi G., Travis J. M. J., Palmer S. C. F., Ancrenaz M., et al. (2021). Orangutan movement and population dynamics across human-modified landscapes: implications of policy and management. Landscape Ecol. 36, 2957–2975. doi: 10.1007/s10980-021-01286-8
Seiler N., Robbins M. M. (2015). Ranging on community land and crop-raiding by Bwindi Gorillas. Gorilla J. 50.
Seiler N., Robbins M. M. (2016). Factors influencing ranging on community land and crop raiding by mountain gorillas. Anim. Conserv. 19, 176–188. doi: 10.1111/acv.12232
Sharma N., Huffman M. A., Gupta S., Nautiyal H., Mendonça R., Morino L., et al. (2016). Watering holes: The use of arboreal sources of drinking water by Old World monkeys and apes. Behav. Processes 129, 18–26. doi: 10.1016/j.beproc.2016.05.006
Sheil D., Puri R., Wan M., Basuki I., van Heist M., Liswanti N., et al. (2006). Recognizing local people’s priorities for tropical forest biodiversity. Ambio 35, 17–24. doi: 10.1579/0044-7447-35.1.17
Sheil D., Sanz N., Lewis R., Mata J., Connaughton C. (2017). “Exploring local perspectives and preferences in forest landscapes: Towards democratic conservation,” in Tropical forest conservation: Long-term processes of human evolution, cultural adaptations and consumption patterns (Mexico City: UNESCO), 262–283.
Shively C. A., Day S. M. (2015). Social inequalities in health in nonhuman primates. Neurobiol. Stress 1, 156–163. doi: 10.1016/j.ynstr.2014.11.005
Siddiq M., Uebersax M. A., Siddiq F. (2022). “Global production, trade, processing and nutritional profile of dry beans and other pulses,” in Dry Beans and Pulses. Eds. Siddiq M., Uebersax M. A.. (Chichester, UK: Wiley Blackwell) 1–28.
Stevenson J. R., Villoria N., Byerlee D., Kelley T., Maredia M. (2013). Green Revolution research saved an estimated 18 to 27 million hectares from being brought into agricultural production. Proc. Natl. Acad. Sci. 110, 8363–8368. doi: 10.1073/pnas.1208065110
Strindberg S., Maisels F., Williamson E. A., Blake S., Stokes E. J., Aba’a R., et al. (2018). Guns, germs, and trees determine density and distribution of gorillas and chimpanzees in Western Equatorial Africa. Sci. Adv. 4, eaar2964. doi: 10.1126/sciadv.aar2964
Struebig M. J., Fischer M., Gaveau D. L. A., Meijaard E., Wich S. A., Gonner C., et al. (2015). Anticipated climate and land-cover changes reveal refuge areas for Borneo’s orang-utans. Global Change Biol. 21, 2891–2904. doi: 10.1111/gcb.12814
Sultan B., Gaetani M. (2016). Agriculture in West Africa in the twenty-first century: climate change and impacts scenarios, and potential for adaptation. Front. Plant Sci. 7. doi: 10.3389/fpls.2016.01262
Terasaki Hart D. E., Yeo S., Almaraz M., Beillouin D., Cardinael R., Garcia E., et al. (2023). Priority science can accelerate agroforestry as a natural climate solution. Nat. Climate Change. doi: 10.1038/s41558-023-01810-5
The World Bank (2022a) Prevalence of undernourishment (% of population) - Sub-Saharan Africa. Available at: https://data.worldbank.org/indicator/SN.ITK.DEFC.ZS?locations=ZG.
The World Bank (2022b) Rural population growth (annual %) - Sub-Saharan Africa. Available at: https://data.worldbank.org/indicator/SP.RUR.TOTL.ZG?locations=ZG.
Tranquilli S., Abedi-Lartey M., Amsini F., Arranz L., ASamoah A., Babafemi O., et al. (2012). Lack of conservation effort rapidly increases African great ape extinction risk. Conserv. Lett. 5, 48–55. doi: 10.1111/j.1755-263X.2011.00211.x
Tweh C. G., Lormie M. M., Kouakou C. Y., Hillers A., Kühl H. S., Junker J. (2015). Conservation status of chimpanzees Pan troglodytes verus and other large mammals in Liberia: a nationwide survey. Oryx 49, 710–718. doi: 10.1017/S0030605313001191
Twinamatsiko M., Baker J., Harrison M., Shirkhorshidi M., Bitariho R., Wieland M., et al. (2014). Linking Conservation, Equity and Poverty Alleviation Understanding profiles and motivations of resource users and local perceptions of governance at Bwindi Impenetrable National Park, Uganda. (London, UK: International Institute for Environment and Development)
Umar H. Y., Giroh D. Y., Agbonkpolor N. B., Mesike C. S. (2011). An overview of world natural rubber production and consumption: an implication for economic empowerment and poverty alleviation in Nigeria. J. Hum. Ecol. 33, 53–59. doi: 10.1080/09709274.2011.11906350
UNDESA (2019). World Urbanization Prospects: The 2018 revision (New York: United Nations Department of Economic and Social Affairs).
van Ittersum M. K., van Bussel L. G. J., Wolf J., Grassini P., van Wart J., Guilpart N., et al. (2016). Can sub-Saharan Africa feed itself? Proc. Natl. Acad. Sci. 113, 14964–14969. doi: 10.1073/pnas.1610359113
Vermeulen S., Sheil D. (2007). Partnerships for tropical conservation. Oryx 41, 434–440. doi: 10.1017/S0030605307001056
Vise-Thakor R. (2022)Sanctuaries in Africa face water shortages. In: . Available at: https://pasa.org/awareness/sanctuaries-in-africa-face-water-shortages/.
Weng L., Boedhihartono A. K., Dirks P. H. G. M., Dixon J., Lubis M. I., Sayer J. A. (2013). Mineral industries, growth corridors and agricultural development in Africa. Global Food Secur. 2, 195–202. doi: 10.1016/j.gfs.2013.07.003
West T. A. P., Wunder S., Sills E. O., Börner J., Rifai S. W., Neidermeier A. N., et al. (2023). Action needed to make carbon offsets from forest conservation work for climate change mitigation. Science 381, 873–877. doi: 10.1126/science.ade3535
Wich S. A., Garcia-Ulloa J., Kühl H. S., Humle T., Lee J. S. H., Koh L. P. (2014). Will oil palm’s homecoming spell doom for Africa’s great apes? Curr. Biol. 24, 1659–1663. doi: 10.1016/j.cub.2014.05.077
Wilcove D. S., Giam X., Edwards D. P., Fisher B., Koh L. P. (2013). Navjot’s nightmare revisited: logging, agriculture, and biodiversity in Southeast Asia. Trends Ecol. Evol. 28, 531–540. doi: 10.1016/j.tree.2013.04.005
Williams D. R., Alvarado F., Green R. E., Manica A., Phalan B., Balmford A. (2017). Land-use strategies to balance livestock production, biodiversity conservation and carbon storage in Yucatán, Mexico. Glob Chang Biol. 23, 5260–5272. doi: 10.1111/gcb.13791
Williams D. R., Clark M., Buchanan G. M., Ficetola G. F., Rondinini C., Tilman D. (2021). Proactive conservation to prevent habitat losses to agricultural expansion. Nat. Sustainability 4, 314–322. doi: 10.1038/s41893-020-00656-5
World Bank, Government of Rwanda (2020). Future Drivers of Growth in Rwanda: Innovation, Integration, Agglomeration, and Competition (Washington, DC: World Bank).
Wright E., Eckardt W., Refisch J., Bitariho R., Grueter C. C., Ganas-Swaray J., et al. (2022). Higher Maximum Temperature Increases the Frequency of Water Drinking in Mountain Gorillas (Gorilla beringei beringei). Front. Conserv. Sci. 3. doi: 10.3389/fcosc.2022.738820
Wunder S. (2005). Payments for Environmental Services: Some nuts and bolts. Center for International Forestry Research Occasional Paper No. 42 (Bogor, Indonesia: Center for International Forestry Research).
You L., Wood-Sichra U., Fritz S., Guo Z., See L., Koo J. (2017) Spatial Production Allocation Model (SPAM) 2005 v3.2. 2017. Available at: http://mapspam.info.
Zemp D. C., Guerrero-Ramirez N., Brambach F., Darras K., Grass I., Potapov A., et al. (2023). Tree islands enhance biodiversity and functioning in oil palm landscapes. Nature 618, 316–321. doi: 10.1038/s41586-023-06086-5
Zenna N., Senthilkumar K., Sie M. (2017). “Rice production in Africa,” in Rice Production Worldwide. Eds. Chauhan B. S., Jabran K., Mahajan G. (Cham: Springer International Publishing), 117–135.
Keywords: conservation, conservation finance, crop foraging, food security, food systems, great apes, poverty, rural development
Citation: Meijaard E, Unus N, Ariffin T, Dennis R, Ancrenaz M, Wich S, Wunder S, Goh CS, Sherman J, Ogwu MC, Refisch J, Ledgard J, Sheil D and Hockings K (2023) Apes and agriculture. Front. Conserv. Sci. 4:1225911. doi: 10.3389/fcosc.2023.1225911
Received: 20 May 2023; Accepted: 09 October 2023;
Published: 09 November 2023.
Edited by:
Maria Cristina Duarte, University of Lisbon, PortugalReviewed by:
Andreia Garces, University of Trás-os-Montes and Alto Douro, PortugalMaria Joana Ferreira Da Silva, Centro de Investigacao em Biodiversidade e Recursos Geneticos (CIBIO-InBIO), Portugal
Copyright © 2023 Meijaard, Unus, Ariffin, Dennis, Ancrenaz, Wich, Wunder, Goh, Sherman, Ogwu, Refisch, Ledgard, Sheil and Hockings. This is an open-access article distributed under the terms of the Creative Commons Attribution License (CC BY). The use, distribution or reproduction in other forums is permitted, provided the original author(s) and the copyright owner(s) are credited and that the original publication in this journal is cited, in accordance with accepted academic practice. No use, distribution or reproduction is permitted which does not comply with these terms.
*Correspondence: Erik Meijaard, emeijaard@borneofutures.org
†These authors have contributed equally to this work