Binturong ecology and conservation 223
binturongs had a third activity peak around noon (Δ1 = 0.636;SE = 0.099;P = 0.062). Other disturbance and human-associated variables showed similar impacts on the diel activity of binturongs (Supplementary Figs 5 & 6).
Discussion
PLATE 1 Camera-trap image of a binturong Arctictis binturong in Danum Valley, Malaysian Borneo.
edge performed worse than the null model, suggesting no local-scale habitat associations with those variables (Supplementary Table 7).
Diel activity patterns
We analysed the diel activity of binturongs from camera- trap data. Pooling all observations, the kernel density esti- mation showed a crepuscular trend, with peaks in activity before sunrise and after sunset (Fig. 3a; Supplementary Fig. 5a,b). There was substantial variability in the activity patterns across sampling units with moderate overlap (Δ1 = 0.338–0.748) but no clear pattern for differences (Anderson–Darling k-sample test = 3.036;P= 0.733). In the more intact forests that were .1 km from edges,
This multiscale synthesis of binturongs largely failed to find significant habitat associations with habitat degradation and suggests binturongs demonstrate more habitat plasticity than previously thought. However, binturongs never per- sisted in small forest patches (,10 km2), which could ex- plain why we did not record them in Singapore, although the common palm civet Paradoxurus hermaphroditus and other large herbivores persist there (Dehaudt et al., 2022; Lamperty et al., 2023). In more highly forested land- scapes, binturongs were equally common in intact and de- graded/logged forests and interior forest and habitats near forest edges. The species’ avoidance of oil palm plantations at the landscape and local scales contradicted our hypothesis and differs from other crop-using frugivores such as pigs (Sus scrofa and Sus barbatus), macaques (Macaca ne- mestrina and Macaca fascicularis) and other civet species (Luskin et al., 2017; Dehaudt et al., 2022). Binturongs altered their diel activity at forest edges and in disturbed forests to become more nocturnal, suggesting a behavioural adapta- tion to avoid people (Negret et al., 2023). We conclude that where sufficient forest cover is retained in the larger landscapes (i.e. .40%in a 1,256-km2 area), binturongs
FIG. 2 Variation in binturong detections amongst the landscapes assessed in this study, and local occupancy (Table 1). Binturong captures are shown in relation to (a) % of the area within a 20-km radius covered by oil palm plantations and (b) the forest intactness within a 20-km radius. Data points show raw capture data (jittered for clarity; red points indicate zero detections). Predicted occupancy is shown in relation to (c) elevation, (d) distance to the nearest river and (e) % of the area within a 1-km radius covered by oil palm plantations.We centred and standardized all covariates prior to modelling, so that effect sizes can be compared.We calculated P-values based on the covariate z-values. Trend lines in all panels were drawn using the predict() function in R and grey areas represent the 95% confidence intervals.We assessed landscape-scale trends using zero-inflated Poisson generalized linear mixed models (a,b) and local-scale trends using hierarchical occupancy models (c–e).
Oryx, 2024, 58(2), 218–227 © The Author(s), 2023. Published by Cambridge University Press on behalf of Fauna & Flora International doi:10.1017/S0030605322001491
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