Land-use change pushes biodiversity into human-modified landscapes, where native ecosystems are surrounded by anthropic land covers (ALCs). Yet, the ability of species to use these emerging covers remains poorly understood. We quantified the use of ALCs by primates worldwide, and analyzed species’ attributes that predict such use. Most species use secondary forests and tree plantations, while only few use human settlements. ALCs are used for foraging by at least 86 species with an important conservation outcome: those that tolerate heavily modified ALCs are 26% more likely to have stable or increasing populations than the global average for all primates. There is no phylogenetic signal in ALCs use. Compared to all primates on Earth, species using ALCs are less often threatened with extinction, but more often diurnal, medium or large-bodied, not strictly arboreal, and habitat generalists. These findings provide valuable quantitative information for improving management practices for primate conservation worldwide.
With ~70% of all terrestrial ecosystems currently altered by human activities1, the preservation of biodiversity and ecosystem functions is challenging2, particularly in the tropics3. As a consequence of land-use change, an increasing number of species are being “forced” to inhabit human-modified landscapes, which are constituted by a mosaic of different land covers, both natural and anthropic. The ability of organisms to use anthropic land covers (ALCs) is rapidly becoming a key determinant of their persistence in human-modified landscapes3,4. Therefore, a better understanding of how and why some species use different types of ALCs is urgently needed to better predict and manage biodiversity in the Anthropocene5.
Traditionally, the ALCs surrounding remnants of natural vegetation are referred to as the matrix4,6. However, rather than being regarded as a homogeneous land cover of unsuitable habitat, as assumed in early classical models7,8, the anthropic matrix should be viewed as a collection of different ALCs, many of which can be used by species for different purposes, including foraging, dispersal, and reproduction6,9. In fact, there is evidence for birds, frogs, small mammals, and ants showing that the higher the ability of a species to use ALCs, the lower their probability of becoming extinct in fragmented landscapes9,10,11. In other words, patch-dependent species typically have higher extinction thresholds12, meaning they require larger amounts of unmodified habitat to avoid extinction13. Unfortunately, for many species, studies mostly focus on their ecology within their primary habitat, especially in protected areas14, thus limiting our understanding of their use of and tolerance to ALCs. This information is urgently needed to shed light on many theoretical debates about the main drivers of biodiversity patterns in human-modified landscapes.
The predominance of the habitat–matrix paradigm (i.e., binary landscapes comprised of either habitat or nonhabitat) in landscape ecology has been strongly criticized15,16 and is gradually being replaced by approaches based on heterogeneous landscapes17,18. Emerging ecological approaches, such as “countryside biogeography”19 and different theoretical models20,21 and debates (e.g., land-sharing vs. land-sparing debate22,23) are based on the premise that the matrix is in fact heterogeneous, and that each ALC type may span a spectrum of species-specific ecological value. To better understand species’ responses to landscape changes we need to assess the ecological role of each land cover (e.g., provision of food, refuge, and nesting sites) to be able to design functional landscapes18. This information can be used to improve management and conservation strategies. For instance, if species are relatively resilient to changes in their habitat and able to use resources in ALCs, they will fare better with a land-sharing approach that limits land-use intensification at the potential cost of increased habitat conversion24. Alternatively, if species are highly sensitive to habitat changes and are unable to use ALCs, a land-sparing approach will be more effective as it maximizes natural habitat conservation while concentrating production elsewhere22.
Nonhuman primates (primates, hereafter) are particularly susceptible to land-use changes25, which threaten ~60% (n = 278 species) of the world’s 504 species with extinction26. As most primate species are forest-specialists, particularly in the Neotropics27 forest loss is considered a main threat to primate conservation28. There are, though, many local, and landscape characteristics that may help reduce the impact of habitat loss on primate survival in human-modified landscapes29. However, most research has focused on assessing the effects of the characteristics of natural vegetation remnants on primate diet, behavior, and demography30. While primates are known to use some types of ALCs31,32,33, the available evidence is widely scattered and the global patterns of use remain unknown beyond a qualitative level. Further, no comprehensive effort exists to link primates’ ecological traits to the extent of use of specific ALCs, greatly limiting our ability to predict the impact of specific landscape-management strategies on these mammals.
Here, we provide quantitative evidence regarding which types of ALCs are most frequently used by primates and for what activities. We also evaluate whether there are certain characteristics of the species, such as conservation status, ecological traits, and/or phylogenetic relationships that may help us predict their use of ALCs. We address these questions by reviewing 468 records of ALC use by primates. We focus on the most common ALC types in human-modified landscapes, including human settlements, open areas (i.e., annual crops and cattle pastures), tree plantations, connectors (i.e., isolated trees and linear landscape elements such as live fences and hedgerows), and secondary forests (i.e., regenerating forests following the removal of native vegetation). We compare the characteristics of species using these ALCs with the expected values based on all of the world’s primates. The primate characteristics considered were conservation status (IUCN conservation category and population trends), ecological traits (diel activity, locomotion, trophic guild, body mass, and forest specialization), and phylogenetic relationships.
Results and Discussion
Use of anthropic land covers by primates
We found positive evidence that at least 147 primate species (~30% of 504 primate species on Earth) use at least one of the five ALC types, with 60 genera (out of 82 genera in the world, ~75%) and all 15 families represented. Use of ALCs was evident worldwide (Fig. 1a), but the percentage of species was significantly higher than expected by chance in mainland Africa, and lower than expected in Madagascar (chi-squared test, χ2 = 15.78, P = 0.001; Fig. 1b). Different ALC types varied in the number of species using them (χ2 = 20.64, P < 0.001; Fig. 1c): secondary vegetation was used by the highest number of species (79) and human settlements were used by the lowest (34). This is not surprising, as these two types of ALC represent two extremes in a gradient of habitat modification. This pattern was particularly evident in the Neotropics and in Madagascar (Fig. 1d), where most species are strictly arboreal. On the other hand, a higher proportion of primates from mainland Africa were recorded using human settlements and open areas and a higher proportion of primates from Asia used tree plantations, human settlements, and open areas such as annual crops and cattle pastures (Fig. 1d). This is probably because many primate species in these two biogeographic realms have both arboreal and terrestrial locomotion modes. In some regions of these realms this pattern can also be caused by peoples’ perception of primates as sacred animals, which favors their persistence in human-dominated environments34,35.
All ALC types were used for foraging, resting, and traveling (Fig. 2). Human settlements and secondary forests were mostly used for either foraging or all activities combined, suggesting that these ALCs can be used as temporary or permanent habitats under certain conditions. Although most studies did not report if the species were using ALCs as habitat, at least 86 species (17% of all primates on Earth) are actively obtaining food resources from ALCs, highlighting their importance for primate conservation32,36. In the case of forest-specialist primates, which represent 70% of the studied species, these results suggest that they can supplement their diet by foraging in ALCs—a process referred to as landscape supplementation20. Connectors, such as living fences and isolated trees, supported primate foraging for 24 species, but almost half of the records were for travel alone, demonstrating the important role of these ALCs in increasing landscape connectivity32,37,38. An important next step will be to assess which species can maintain their populations solely in ALCs, which species are strongly dependent on their natural habitats, and which ones may survive in natural habitat patches with some degree of landscape supplementation in ALCs.
Conservation signal in the use of anthropic covers
We found a significant, positive relationship between the use of ALCs and both conservation status and population trend (IUCN red list39; IUCN 2017 Fig. 3). The proportion of species classified as least concern was significantly higher in the group of primates recorded using ALCs, compared to all primates, particularly in human settlements (χ2 = 18.95, P < 0.001). Nearly half of all species recorded using ALCs were classified as vulnerable, endangered, or critically endangered by the IUCN (Fig. 3a), suggesting that ALC use alone does not necessarily prevent endangerment. Although use of ALCs may favor primate persistence in human-modified landscapes, it is important to recognize that their use also exposes primates to important threats, such as hunting, road kills, predation, and infectious diseases40,41,42.
About 80% of all species using ALCs showed declining population sizes (Fig. 3b). Nonetheless, ALC use seems to soften this pattern, as we found a lower proportion of species with decreasing populations using ALCs than would be expected based on the world’s primates. The latter pattern was particularly strong for primates using human settlements (χ2 = 25.52, P < 0.001) and open areas (χ2 = 10.67, P = 0.005). These results suggest that species able to use highly modified ALC types have a higher probability of persisting in anthropogenic tropical landscapes.
Ecological traits that predict the use of anthropic covers
We found significant associations between the ecological traits of primates and their use of ALCs (Fig. 4). In particular, nocturnality was less frequent among species using ALCs, especially in open areas (χ2 = 13.88, P < 0.001), secondary forest (χ2 = 11.58, P = 0.003), connectors (χ2 = 9.62, P = 0.008), and human settlements (χ2 = 8.52, P = 0.014; Fig. 4a). We would have expected a higher (not lower) incidence of nocturnality among species using ALCs because nocturnal primates are less likely to encounter humans, and thus, they could perceive ALCs as less dangerous, compared to diurnal primates43. Yet, nocturnal primates are all forest-specialists, arboreal and with small-to-medium body mass—ecological traits that together seem to limit the use of ALCs (see below).
Strictly arboreal species were less frequent in the group of primates using ALCs, particularly among those using human settlements (χ2 = 19.66, P < 0.001) and open areas (χ2 = 13.95, P < 0.001; Fig. 4b). Similarly, there was also a lower proportion of small-bodied species using ALCs than expected by chance, particularly, once again, among those using human settlements (χ2 = 12.43, P = 0.002) and open areas (χ2 = 19.01, P < 0.001; Fig. 4c). The latter result is not surprising as small-bodied species are more likely to be arboreal, which limits their movement into treeless areas. Also, small primates tend to have smaller home ranges44, and thus, they can be able to inhabit smaller habitat remnants without using resources from ALCs. This may lower the probability of observing them in ALCs, especially in landscapes with a relatively recent history of anthropic land use (e.g., <30 y). Although this finding does not mean that small primates have lower extinction risk in human-modified landscapes45, our results point in this direction, as 57.3% of large ALC-tolerant species (n = 21 species) are threatened with extinction, whereas 49.9% of small-bodied species (n = 42) are threatened (Supplemntary Table 1). In contrast, other studies suggest that those species that avoid using ALCs can be more prone to extinction in these emerging landscapes;10,46,47 thus, additional primate studies are needed to accurately assess the effect of body weight on extinction risk.
Forest-specialists were present in all land cover types, but they were less frequent among ALC-tolerant species (χ2 = 11.19, P = 0.003), particularly in human settlements (χ2 = 31.53, P < 0.001) and open areas (χ2 = 11.76, P = 0.003) (Fig. 4d). Although primate trophic guild was not significantly related to the use of ALCs, there was a trend toward a higher proportion of omnivorous species in human settlements than expected (Supplementary Fig. 1). These results, together with the fact that strictly arboreal species were less frequent in ALCs, suggest that the more generalist a species is, especially in terms of habitat and/or locomotion, the more resilient it is to habitat disturbance; a finding consistent with previous studies46,47,48.
Phylogenetic signal in ALC use
We found a very weak phylogenetic signal in the use of ALCs (Fig. 5), where it was neither clustered nor randomly distributed across the phylogenetic tree (D = 0.83; P [D = 0] < 0.001; P [D = 1] = 0.001). The sensitivity analyses revealed that removing Cercopithecidae, the primate family with the largest number of species analyzed, did not influence the estimates of phylogenetic signal. However, the removal of sportive lemurs (family Lepilemuridae) significantly influenced our estimates of phylogenetic signal, despite having a similar number of species to most other families (see Supplementary Note 1). In particular, our results indicate that most species in this primate family (Lepilemuridae) do not use ALCs, i.e., nonuse of ALCs is a phylogenetically conserved characteristic for this clade. The highly conserved morphology and shared ecological traits (e.g., arboreal locomotion, nocturnal activity, and forest specialization) within this family49 could explain this pattern. In contrast, the behavioral and ecological traits that could make a species tolerant to ALC conditions vary in their degree of phylogenetic conservatism50. This, together with the widespread alteration of primates’ habitats, leads to a pattern in which the use of ALCs is unpredictable in relation to species’ evolutionary relationships.
Given the ongoing loss and alteration of primates’ natural habitats, knowledge about how and why some species are able to use ALCs is essential to propose effective conservation strategies in human-modified landscapes. We provide a comprehensive quantification of the use of five dominant types of ALCs by primates worldwide. We also provide a global assessment of the relationships between primate use of ALCs and primates’ ecological traits, conservation status and phylogenetic relationships. Our findings highlight the fact that ALCs can play important roles for the conservation of many primate species in anthropogenic landscapes, providing food resources, refuge and opportunities for dispersal. We note, however, that for 70% of the primates on Earth, we found no evidence of ALC use, suggesting that benefits associated with the use of ALCs are limited to some species, in which case they are unlikely to prevent the current extinction crisis of the world’s primates26. While some poorly studied species might also be able to exploit ALCs, many other species are likely to depend on remnants of their primary habitat for their long-term conservation. Also, the use of ALCs can have negative effects on primates’ populations, as it increases both exposure to several threats and occurrence of conflicts with humans due to crop raiding, aggression, or disease transmission40,41,42. Thus, although priority conservation actions should focus on the maintenance of primary habitats for primates and other vertebrate taxa9, they can be complemented with other land-management strategies, such as replacing highly modified ALCs by more functional land covers that provide resources for wildlife and/or facilitate their movement between habitat patches. Such an integrative approach will enhance the conservation value of increasingly modified landscapes for our closest relatives.
Evidence of ALC use by primates
We systematically searched for articles published up to November 2, 2016, using the following search term sequence in ISI Web of Knowledge (www.isiwebofknowledge.com), SciVerse SCOPUS (www.scopus.com) and Google Scholar (https:// scholar.google.com.br/) databases: [(primate* OR monk*) AND (“plantation” OR “crop” OR “agroecosystem” OR “cultivation” OR “agriculture” OR “regenerating forest” OR “regenerating vegetation” OR “secondary forest” OR “secondary vegetation” OR “second growth” OR “clear cut” OR “life fence” OR “isolated trees” OR “scattered trees” OR “remnant trees” OR “corridor” OR “fencerow” OR “corridor line” OR “bridge” OR “stepping stones” OR “fence” OR “connectivity” OR “hedgerow” OR “strip” OR “city” OR “urban” OR “human settlement” OR “village” OR “settlement” OR “pasture” OR “grazing line” OR “ground” OR “cattle” OR “ground”) AND/OR (“fragmentation” OR “landscape”)]. These keywords were searched across all reference topics, except in Web of Knowledge where searches were restricted to title, abstract and keywords of articles. We then conducted additional searches in Google Scholar using keywords translated into Portuguese, Spanish and French, including the grey literature (e.g., MSc and PhD theses and unpublished reports). We classified all hits obtained into five groups, depending on the type of ALC used by primates: (i) human settlements (i.e., any kind of urban environment such as cities, towns, or villages), (ii) open areas (i.e., annual crops and cattle pastures), (iii) tree plantations (including all types of agroforestry systems), (iv) connectors (i.e., isolated trees and linear landscape elements, such as vegetation corridors, live fences and hedgerows), and (v) secondary forests (i.e., regenerating forests following regrowth after an acute disturbance event, such as logging and deforestation). We excluded review articles and studies with captive or reintroduced animals. Because for some ALCs the available literature is scarce, we selected the most recent 60 studies per each ALC type. Nevertheless, as some studies included information about more than one ALC type, the final database included 258 independent studies (Supplementary Table 1) containing 468 records of 147 primate species using ALCs. Such records span 44 countries from four biogeographic realms: mainland Africa (17 countries), Madagascar, Asia (13 countries), and the Neotropics (13 countries).
From each study, we obtained, for each primate species, the scientific name and family, geographic coordinates and country, and the activity recorded within the ALC (i.e., traveling, resting, foraging, or all activities). Traveling refers to movements within and between ALC types. Resting refers to short/long diurnal/nocturnal rests, and foraging refers to the procurement, acquisition and/or ingestion of food. We assumed that resting and foraging require travel to reach any given destination. Therefore, the category of “all activities” included studies that reported observations on all three main activities, or resting and foraging, in an ALC. As most studies did not report extended information about the use of each ALC, we cannot know if primates are using it as habitat. Information about the surrounding landscape, such as distance to the nearest edge, proportion of remaining primary habitat, were not reported in the vast majority of studies, thereby precluding analyses related to these types of information. Furthermore, although studies reported general coordinates of the study sites, most did not report the coordinates where the individuals were recorded in an ALC, limiting our capacity to assess the landscape context.
Conservation and ecological predictors
For each primate species we obtained the conservation status, the population trend, and whether they are forest-specialists or not, from the International Union for Conservation of Nature (IUCN) database in the “letsR”52 package for R, version 3.0.153. Regarding ecological traits, we considered: locomotion mode (i.e., arboreal, terrestrial or both), diel activity (i.e., diurnal, nocturnal, or cathemeral), and body mass and trophic guild. Although body mass is a morphological trait, we considered it as an ecological trait because of its very high-ecological significance. For instance, it is positively related to home range size, thus affecting the way species interact with their environment44,54. Body mass was categorized into three classes: small (<2 kg), medium (2–10 kg), and large (>10 kg). Trophic guilds included six general groups: frugivorous (>60% of fruits in diet), folivorous (>60% leaves in diet), folivorous–frugivorous (diet comprised of both fruits and leaves in similar proportions), omnivorous (both plants and animals in diet), insectivorous (diet dominated by arthropods), and gummivorous (diet dominated by plant exudates). Ecological trait data was primarily extracted from Mittermeier et al.27. When some of the ecological traits were not reported in this encyclopedia, we actively searched for information in the literature. When the trait was reported in other scientific articles or databases, we searched for 1–3 references (depending on availability) and we used mean or modal values55. In total, we reviewed 370 studies, most of them published in peer-reviewed scientific journals and books. For each specific datum we included the corresponding reference. The database was carefully checked for possible errors. When a specific datum was considered nonreliable (e.g., very extreme or contradictory values and values obtained with questionable methodology) we did not include it in the database. To assess relationships between primate characteristics and ALC use, we used goodness of fit chi-square tests. We selected this analysis because it is particularly recommended to compare observed vs. expected frequencies. In particular, we compared the number of species with each trait between those species that were observed using ALCs and the expected values based on all of the world’s primates. We excluded from analyses species for which there was no available information.
To quantify phylogenetic signal in ALCs use, we used published phylogenetic relationships and divergence times from a molecular timetree built using 79 gene segments for 372 species (367 primates and 5 outgroup species) and 8 fossil-calibrated nodes50, 51. Specifically, we used the timetree built considering autocorrelated rates of molecular evolution (identified by Bayesian model selection as fitting the data better than a model with independent rates), and a conservative interpretation of both the age and the placement of key fossils with the living primate radiation. Of the 367 species included in this phylogeny, we retained 352 after standardizing synonyms and dropping infraspecific taxa.
To explore how phylogeny might capture species differences in ALCs use, we calculated the D statistic56. D measures phylogenetic signal strength in binary traits. Values of D are scaled to set points of 0.0 (trait values phylogenetically conserved as expected under a Brownian Motion threshold model) and 1.0 (trait values distributed randomly across the phylogeny). For significance testing, the observed distribution of trait values at the tips of the tree was compared to both randomly shuffled values and the expected values from a Brownian Motion threshold model. For all tests of phylogenetic signal, we used the phylo.d function in the R package “caper”57. We used 9999 permutations to estimate the probability of the observed value of D under null models of both no phylogenetic structure and Brownian motion.
To investigate the nonrandom but weak result we found for the Order as a whole, we tested whether certain clades were driving relatively large changes in our estimates of phylogenetic signal. We adapted the framework provided in the “sensiPhy”59 package to perform sensitivity analyses and tested how excluding families (with ten or more species) from the analyses would influence the estimates of phylogenetic signal. When the removal of a clade leads to a large change in the estimate of D, it can be considered to be influential. To correct for clade size, we used randomization tests to determine if the change in parameter estimates is significantly different from a null distribution created by randomly removing the same number of species as the focal clade (Supplementary Table 2, Supplementary Fig. 2).
Further information on experimental design is available in the Nature Research Reporting Summary linked to this article.
All data generated or analyzed during this study are included in this published article or its Supplementary Information Files.
Ellis, E. C. et al. Used planet: a global history. Proc. Natl Acad. Sci. USA 110, 7978–7985 (2013).
Newbold, T. et al. Global effects of land use on local terrestrial biodiversity. Nature 520, 45 (2015).
Gardner, T. A. et al. Prospects for tropical forest biodiversity in a human-modified world. Ecol. Lett. 12, 561–582 (2009).
Watling, J. L. et al. Meta-analysis reveals the importance of matrix composition for animals in fragmented habitat. Glob. Ecol. Biogeogr. 20, 209–217 (2011).
Corlett, R. T. The Anthropocene concept in ecology and conservation. Trends Ecol. Evol. 30, 36–41 (2015).
Prevedello, J. A. & Vieira, M. V. Does the type of matrix matter? A quantitative review of the evidence. Biodivers. Conserv. 19, 1205–1223 (2010).
MacArthur, R. H. & Wilson, E. O. The Theory of Island Biogeography. (Princeton University Press, 1967).
Haila, Y. A conceptual genealogy of fragmentation research: from island biogeography to landscape ecology. Ecol. Appl. 12, 321–334 (2002).
Ferreira, A. S., Peres, C. A., Bogoni, J. A. & Cassano, C. R. Use of agroecosystem matrix habitats by mammalian carnivores (Carnivora): a global‐scale analysis. Mammal. Rev. 48, 312–327 (2018).
Gascon, C. et al. Matrix habitat and species richness in tropical forest remnants. Biol. Conserv. 91, 223–229 (1999).
Boesing, A. L., Nichols, E. & Metzger, J. P. Biodiversity extinction thresholds are modulated by matrix type. Ecography 41, 1520–1533 (2018).
Fahrig, L. Effect of habitat fragmentation on the extinction threshold: a synthesis. Ecol. Appl. 12, 346–353 (2002).
Fahrig, L. How much habitat is enough? Biol. Conserv. 100, 65–74 (2001).
Martin, L. J., Blossey, B. & Ellis, E. Mapping where ecologists work: biases in the global distribution of terrestrial ecological observations. Front. Ecol. Environ. 10, 195–201 (2012).
Franklin, J. F. & Lindenmayer, D. B. Importance of matrix habitats in maintaining biological diversity. Proc. Natl Acad. Sci. USA 106, 349–350 (2009).
Mendenhall, C. D., Karp, D. S., Meyer, C. F. J., Hadly, E. A. & Daily, G. C. Predicting biodiversity change and averting collapse in agricultural landscapes. Nature 509, 213–217 (2014).
Bennett, A. F., Radford, J. Q. & Haslem, A. Properties of land mosaics: implications for nature conservation in agricultural environments. Biol. Conserv. 133, 250–264 (2006).
Fahrig, L. et al. Functional landscape heterogeneity and animal biodiversity in agricultural landscapes. Ecol. Lett. 14, 101–112 (2011).
Daily, G. C. in Nature and Human Society: the Quest for a Sustainable World (ed. P. H. Raven) 104–113 (National Research Council, National Academy Press, 1997).
Dunning, J. B., Danielson, B. J. & Pulliam, H. R. Ecological processes that affect populations in complex landscapes. Oikos 65, 169–175 (1992).
Tscharntke, T. et al. Landscape moderation of biodiversity patterns and processes—eight hypotheses. Biol. Rev. 87, 661–685 (2012).
Green, R. E., Cornell, S. J., Scharlemann, J. P. & Balmford, A. Farming and the fate of wild nature. Science 307, 550–555 (2005).
Law, E. A. & Wilson, K. A. Providing context for the land-sharing and land-sparing debate. Conserv. Lett. 8, 404–413 (2015).
Perfecto, I. & Vandermeer, J. Biodiversity conservation in tropical agroecosystems: a new conservation paradigm. Ann. N. Y. Acad. Sci. 1134, 173–200 (2008).
Marsh, L. K. & Chapman, C. A. Primates in Fragments: Complexity and Resilience. (Springer Science & Business Media, 2013).
Estrada, A. et al. Impending extinction crisis of the world’s primates: why primates matter. Sci. Adv. 3, e1600946 (2017).
Mittermeier, R. A., Rylands, A. B., Hoyo, J. D. & Anandam, M. Handbook of the Mammals of the World—Volume 3. Handbook of the Mammals of the World (Lynx Edicions, 2013).
Arroyo-Rodríguez, V., Galán-Acedo, C. & Fahrig, L. in The international encyclopedia of primatology (ed. Fuentes, A.) 1–10 (Wiley-Blackwell, 2017).
Almeida-Rocha, J. M., Peres, C. A. & Oliveira, L. C. Primate responses to anthropogenic habitat disturbance: a pantropical meta-analysis. Biol. Conserv. 215, 30–38 (2017).
Arroyo-Rodríguez, V. et al. in Primates in Fragments. Developments in Primatology: Progress and Prospects (eds. Marsh, L. K. & Chapman, C. A.) 13–28 (Springer, 2013).
Anderson, J., Rowcliffe, J. M. & Cowlishaw, G. Does the matrix matter? A forest primate in a complex agricultural landscape. Biol. Conserv. 135, 212–222 (2007).
Asensio, N., Arroyo-Rodríguez, V., Dunn, J. C. & Cristóbal-Azkarate, J. Conservation value of landscape supplementation for howler monkeys living in forest patches. Biotropica 41, 768–773 (2009).
Estrada, A., Raboy, B. E. & Oliveira, L. C. Agroecosystems and primate conservation in the tropics: a review. Am. J. Primatol. 74, 696–711 (2012).
Baker, L. R., Tanimola, A. A. & Olubode, O. S. Sacred populations of Cercopithecus sclateri: analysis of apparent population increases from census counts. Am. J. Primatol. 76, 303–312 (2014).
Fargey, P. J. Boabeng–Fiema Monkey Sanctuary—an example of traditional conservation in Ghana. Oryx 26, 151–156 (1992).
Arroyo-Rodríguez, V. et al. Spider monkeys in human-modified landscapes: the importance of the matrix. Trop. Conserv. Sci. 10, 1–13 (2017).
Pozo-Montuy, G. & Serio-Silva, J. C. Movement and resource use by a group of Alouatta pigra in a forest fragment in Balancán, México. Primates 48, 102–107 (2007).
Lees, A. C. & Peres, C. A. Conservation value of remnant riparian forest corridors of varying quality for Amazonian birds and mammals. Conserv. Biol. 22, 439–449 (2008).
IUCN. International Union for Conservation of Nature, IUCN Red List of threatened species. Version 2017 3–4. (2017). Available at: www.iucnredlist.org. Accessed 15 March 2018.
Saj, T. L., Sicotte, P. & Paterson, J. D. The conflict between vervet monkeys and farmers at the forest edge in Entebbe, Uganda. Afr. J. Ecol. 39, 195–199 (2001).
Aghokeng, A. F. et al. Extensive survey on the prevalence and genetic diversity of SIVs in primate bushmeat provides insights into risks for potential new cross-species transmissions. Infect. Genet. Evol. 10, 386–396 (2010).
Priston, N. E., Wyper, R. M. & Lee, P. C. Buton macaques (Macaca ochreata brunnescens): crops, conflict, and behavior on farms. Am. J. Primatol. 74, 29–36 (2012).
Gaynor, K. M., Hojnowski, C. E., Carter, N. H. & Brashares, J. S. The influence of human disturbance on wildlife nocturnality. Science 360, 1232–1235 (2018).
Milton, K. & May, M. L. Body weight, diet and home range area in primates. Nature 259, 459 (1976).
Boyle, S. A. & Smith, A. T. Can landscape and species characteristics predict primate presence in forest fragments in the Brazilian Amazon? Biol. Conserv. 143, 1134–1143 (2010).
Henle, K., Davies, K. F., Kleyer, M., Margules, C. & Settele, J. Predictors of species sensitivity to fragmentation. Biodivers. Conserv. 13, 207–251 (2004).
McKinney, M. L. & Lockwood, J. L. Biotic homogenization: a few winners replacing many losers in the next mass extinction. Trends Ecol. Evol. 14, 450–453 (1999).
Devictor, V., Julliard, R. & Jiguet, F. Distribution of specialist and generalist species along spatial gradients of habitat disturbance and fragmentation. Oikos 117, 507–514 (2008).
Wilmet, L. et al. Field data on the little known and, endangered Lepilemur mittermeieri. J. Primatol. 4, 2 (2015).
Dos Reis, M. et al. Using phylogenomic data to explore the effects of relaxed clocks and calibration strategies on divergence time estimation: primates as a test case. Syst. Biol. https://doi.org/10.1093/sysbio/syy001 (2018).
Vilela, B. & Villalobos, F. LetsR: a new R package for data handling and analysis in macroecology. Methods Ecol. Evol. 6, 1229–1234 (2015).
R Core Team. R version 3.0.1. (2013).
Clutton-Brock, T. H. & Harvey, P. H. in Primate Ecology: Studies of Feeding and Ranging Behaviour in Lemurs, Monkeys and Apes. (ed. Clutton-Brock, T. H.). 557–584 (Academic Press, 1977).
Galán-Acedo, C., Arroyo-Rodríguez, V., & Andresen, E. Ecological traits of the world’s primates database. Zenodo https://doi.org/10.5281/zenodo.1342459 (2018).
Kamilar, J. M. & Cooper, N. Phylogenetic signal in primate behavior, ecology and life history. Philos. Trans. R. Soc. B Biol. Sci. 368, 20120341 (2013).
Fritz, S. & Purvis, A. Selectivity in mammalian extinction risk and threat types: a new measure of phylogenetic signal strength in binary traits. Conserv. Biol. 24, 1042–1051 (2010).
Orme, D. The caper package: comparative analyses in phylogenetics and evolution in R. (2012).
Paterno, G. B., Penone C. & Werner G. D. A. sensiPhy: An r package for sensitivity analysis in phylogenetic comparative methods. Methods Ecol Evol. 9, 1461–1467 (2018).
Pimm, S. et al. The biodiversity of species and their rates of extinction, distribution, and protection. Science 344, 1246752 (2014).
CONACyT (Grant 2015-253946) provided financial support. C.G.-A. received a scholarship from CONACyT (Mexico) and a grant from Rufford (18689-1). We gratefully acknowledge P.A.D. Dias for his valuable and constructive suggestions on the manuscript. We are also grateful for the support provided by the Instituto de Investigaciones en Ecosistemas y Sustentabilidad, UNAM. Part of the writing was done while V.A.-R. was on sabbatical at Carleton University, funded by PASPA-DGAPA-UNAM, and C.G.-A. was on a research visit at the Imperial College London, UK.
The authors declare no competing interests.
Journal peer review information: Nature Communications thanks the anonymous reviewers for their contributions to the peer review of this work. Peer reviewer reports are available.
Publisher’s note: Springer Nature remains neutral with regard to jurisdictional claims in published maps and institutional affiliations.
About this article
Cite this article
Galán-Acedo, C., Arroyo-Rodríguez, V., Andresen, E. et al. The conservation value of human-modified landscapes for the world’s primates. Nat Commun 10, 152 (2019). https://doi.org/10.1038/s41467-018-08139-0
Ecological Applications (2020)
Evaluating extinction debt in fragmented forests: the rapid recovery of a critically endangered primate
Animal Conservation (2020)
Identification of crucial stepping stone habitats for biodiversity conservation in northeastern Madagascar using remote sensing and comparative predictive modeling
Biodiversity and Conservation (2020)
Climatic Change (2020)
Biodiversity and Conservation (2020)