Introduction
Describing which species are threatened, identifying the underlying mechanisms, and then prescribing ways of preventing extinctions are basic challenges for biodiversity conservation (Purvis et al., Reference Purvis, Gittleman, Cowlishaw and Mace2000). The Endangered Egyptian vulture Neophron percnopterus is a migratory, medium-sized raptor whose populations have recently declined throughout its range (IUCN, 2008). The causes driving this decline have been analysed in Italy (Liberatori & Penteriani, Reference Liberatori and Penteriani2001; Sarà & Di Vittorio, Reference Sarà and Di Vittorio2003), Spain (Donázar et al., Reference Donázar, Palacios, Gangoso, Ceballos, González and Hiraldo2002; Carrete et al., Reference Carrete, Grande, Tella, Sánchez-Zapata, Donázar, Diaz-Delgado and Romo2007; Grande et al., Reference Grande, Serrano, Tavecchia, Carrete, Ceballo and Díaz-Delgado2009) and wintering areas in Africa (Grande et al., Reference Grande, Serrano, Tavecchia, Carrete, Ceballo and Díaz-Delgado2009). Factors involved in territory loss in Italy seem primarily related to human threats and reduction in food availability because of decreasing livestock density and/or changes in cattle-raising practices (Liberatori & Penteriani, Reference Liberatori and Penteriani2001; Sarà & Di Vittorio, Reference Sarà and Di Vittorio2003). In peninsular Spain poisoning, the species’ social behaviour and habitat diversity are the most important predictors of territory loss at a landscape scale (Carrete et al., Reference Carrete, Grande, Tella, Sánchez-Zapata, Donázar, Diaz-Delgado and Romo2007). This information can help guide conservation of this species, for which Spain is one of the most important conservation strongholds (IUCN, 2008).
However, insufficient information is available for the management and conservation of the Egyptian vulture at local or regional levels. Lack of such information hinders geographically broad conservation schemes (McAlpine et al., Reference McAlpine, Rhodes, Bowen, Lunney, Callaghan, Mitchell and Possingham2008), and a species can be subject to varying risks of local extinction because of variability in threats across its range (Isaac & Cowlishaw, Reference Isaac and Cowlishaw2004). These two situations may pertain to the Egyptian vulture in Spain, where the species is widely distributed in two bioclimatic regions, the Mediterranean and Euro-Siberian (north-west Spain), and displays differing regional population trends (García-Ripollés & López-López, Reference García-Ripollés and López-López2006; Carrete et al., Reference Carrete, Grande, Tella, Sánchez-Zapata, Donázar, Diaz-Delgado and Romo2007; Mateo-Tomás et al., Reference Mateo-Tomás, Olea and Fombellida2010). Management measures generically recommended in Spain for Egyptian vulture conservation include conservation of communal roosts and rabbit Oryctolagus cuniculus populations (Donázar, Reference Donázar, Madroño, Gonzalez and Atienza2004; Carrete et al., Reference Carrete, Grande, Tella, Sánchez-Zapata, Donázar, Diaz-Delgado and Romo2007). These measures are useful for some Mediterranean populations but not for Euro-Siberian populations, which do not depend on rabbits and do not use roosts regularly (P. Mateo-Tomás & P.P. Olea, unpubl. data). Additionally, disturbance by human activities and wind farms have recently been identified as potentially affecting some Egyptian vulture populations (COCN et al., Reference Donázar, Carrete, de la Riva and Sánchez-Zapata2008; Zuberogoitia et al., Reference Zuberogoitia, Zabala, Martínez and Azcona2008; Mateo-Tomás et al., Reference Mateo-Tomás, Olea and Fombellida2010).
The study reported here focused on the Egyptian vulture population of the Cantabrian Mountains, which support c. 20% of the Spanish population (mostly within the Euro-Siberian region; Mateo-Tomás et al., Reference Mateo-Tomás, Olea and Fombellida2010). Given the global decline of the species, this area may become a key site for its conservation (Gärdenfors, Reference Gärdenfors2001). However, despite the relative stability of this population compared to those in other areas of Spain (Carrete et al., Reference Carrete, Grande, Tella, Sánchez-Zapata, Donázar, Diaz-Delgado and Romo2007), a number of territories have been abandoned since 1997. Here we report our attempt to identify the causes of the abandonment of these territories, which we examined simultaneously at several scales, from nest site to landscape. We also provide recommendations, based on our findings, for management and conservation to prevent further loss of territories.
Study area and species
The study area is on the southern slope of the Cantabrian Mountains (Fig. 1), extending over 8,500 km2 within the Euro-Siberian climatic region and a Euro-Siberian-Mediterranean transition zone running east-west. Extensive livestock farming (i.e. free-ranging cows, sheep and goats at low stocking densities), is the main rural activity. Most Egyptian vulture territories (75%) are located within the Euro-Siberian region. Monitored nests were at altitudes of 670–1,575 m.
Fig. 1 Egyptian vulture territories, centred at the last nest known, in the study area and surroundings. Filled circles are occupied territories (n = 50) and unfilled circles are abandoned territories (n = 14). The dotted line shows the northern border of the study area; squares represent unmonitored territories. The rectangle on the inset indicates the position of the main map in northern Spain.
The Egyptian vulture is a territorial, cliff-nesting raptor distributed from the Mediterranean to India and in Africa. The species is categorized as Endangered in Spain, which now holds the largest population (c. 1,400 breeding pairs) in the occidental Palearctic (Donázar, Reference Donázar, Madroño, Gonzalez and Atienza2004). Breeding pairs arrive from their winter range in Africa in March and remain in their territories until mid September, rearing one or two chicks (Donázar, Reference Donázar1993). The same territory is generally used each year by a pair and is actively defended by its occupants (Donázar, Reference Donázar1993). Breeding dispersal is low (7.5%), and thus territories probably become vacant because of the loss of territory owners without later recruitment, rather than because of territory change (Carrete et al., Reference Carrete, Grande, Tella, Sánchez-Zapata, Donázar, Diaz-Delgado and Romo2007). Although the species is relatively tolerant of human presence (Donázar, Reference Donázar, Madroño, Gonzalez and Atienza2004) it is highly sensitive to poisoning (Grande et al., Reference Grande, Serrano, Tavecchia, Carrete, Ceballo and Díaz-Delgado2009).
Methods
Conceptual model
We designed a multi-scale conceptual model describing the factors influencing the persistence or abandonment of territories by Egyptian vultures (Fig. 2; Table 1). Three scales were considered (nest, cliff and landscape), defined according to species–habitat relationships potentially important for the species. Nest and nesting-cliff scales characterize the nest site, defining the basic reproductive requirements of a breeding pair (Liberatori & Penteriani, Reference Liberatori and Penteriani2001). At the landscape scale we considered three resolutions: a core area (i.e. the area actively defended by a breeding pair) and two home ranges (i.e. the area that is most intensively used by the pair, mainly for foraging; Donázar, Reference Donázar1993). The nest and cliff scales are the most important because, without a cliff with a suitable nest, the other scales would not be relevant. Therefore we modelled nest-site scales together with each of the landscape resolutions (Fig. 2).
Fig. 2 Multi-scale conceptual model of the factors influencing the abandonment of a territory by the Egyptian vulture. This model considered three scales (i.e. nest, cliff and landscape) and three resolutions (i.e. 1-km core area, and 2.5- and 5-km home ranges; see text for details) at the landscape scale. For a description of all 36 variables see Table 1.
Table 1 The 36 variables describing nest-site and landscape characteristics considered potentially to explain territory abandonment by the Egyptian vulture Neophron percnopterus.
1 Digital Elevation Model
2 3rd Spanish Forest Inventory, Ministerio de Medio Ambiente
3 -∑pilogpi, where pi = percentage of surface covered by habitat i
4 1 cow = 5 livestock units; 1 sheep or goat = 1 livestock unit
5 Statistical service of Junta de Castilla y León in León and Palencia
6 National Statistics Institute
Surveys
Egyptian vulture territories were located by a review of previous censuses (Del Moral & Martí, Reference Del Moral and Martí2002; F. Jubete, pers. comm.; authors, unpubl. data), interviews with local shepherds, and field surveys during 2005–2007. We located 80 territories that have been occupied by Egyptian vultures for at least 1 year during 1997–2007. Each territory was mapped using the geographical information system ArcGIS v. 9.0 (ESRI, Redlands, USA). Our final dataset consisted of 50 occupied and 14 abandoned breeding territories that could provide data at the nest-site scale (Fig. 1). Egyptian vulture breeding pairs can use different nests in different years (Donázar, Reference Donázar1993) but such nests are usually close to each other within the same territory (Zuberogoitia et al., Reference Zuberogoitia, Zabala, Martínez and Azcona2008). Therefore, we considered a territory abandoned if it had been occupied for at least 1 year in 1997–1999 but we did not detect Egyptian vultures within the territory in 2005–2007. In our study area the Egyptian vulture has a relatively low detectability (the probability of detecting the species during a visit, if present = 0.44–0.49; authors, unpubl. data). We visited the territories numerous times (mean = 6 visits per territory per year, n = 801 visits) in 2005–2007 to confirm unequivocal occupation or abandonment (95% confidence; authors, unpubl. data). The high quality of the data, especially for abandoned territories, allows accurate predictions despite the unbalanced dataset (Jiménez-Valverde & Lobo, Reference Jiménez-Valverde and Lobo2006). Every visit consisted of the inspection of the territory on days with good visibility, using binoculars and telescopes.
Explanatory variables
We measured a set of variables of potential relevance for the species. Nest location and cliff were described according to morphological features (Table 1). Core area was considered to be the area within a 1-km radius of a nest (Carrete et al., Reference Carrete, Grande, Tella, Sánchez-Zapata, Donázar, Diaz-Delgado and Romo2007). The home range resolutions considered were (1) a 2.5-km radius around the nest (half the average nearest-neighbour distance between territories in the study area; Sarà & Di Vittorio, Reference Sarà and Di Vittorio2003; authors, unpubl. data), and (2) a 5-km radius (double the nearest-neighbour distance, and the territory size recorded in similar areas; Bergier & Cheylan, Reference Bergier and Cheylan1980). We measured 36 variables in five categories: habitat structure, relief, food, inter- and intraspecific interactions and human presence (see Table 1 for hypotheses). The variables were measured in the field or from aerial photographs and detailed maps, and validated by field observations. Because of the high sensitivity of the species to poisoning (Carrete et al., Reference Carrete, Grande, Tella, Sánchez-Zapata, Donázar, Diaz-Delgado and Romo2007) we considered poisoning events within the study area since 2000. These data were obtained at the municipality level from the relevant environmental authorities. We derived three variables with regard to the species implicated in the poisoning event (i.e. mammals, birds or avian scavengers; Table 1) to account for the accessibility of vultures to poison. Climate variables were not included in the analysis because topographic characteristics better summarize microclimatic conditions at the local level (Austin, Reference Austin2002). Feeding stations were not included because, in contrast to other regions (Carrete et al., Reference Carrete, Grande, Tella, Sánchez-Zapata, Donázar, Diaz-Delgado and Romo2007), there are no permanent feeding points in the study area. Similarly, no communal roosts have been reported in the study area (Carrete et al., Reference Carrete, Grande, Tella, Sánchez-Zapata, Donázar, Diaz-Delgado and Romo2007).
Statistical analysis
Linearity was explored by plotting generalized additive models (Hastie & Tibshirani, Reference Hastie and Tibshirani1990) of the response variable (i.e. persistence/abandonment, as 1/0) against every explanatory variable (Table 1). After visual inspection of the resultant plots non-linear relationships were converted into two-piece linear effects by piece-wise regression, in which the explanatory variable is partitioned into intervals and a different linear function is fitted to each interval (Crawley, Reference Crawley2007). The optimal threshold, or the best position of the breakpoint, was selected according to the lowest residual deviance (Crawley, Reference Crawley2007). We used generalized linear models (GLMs) with a binomial error structure to identify those factors influencing territory abandonment.
Models were fitted independently for each scale by performing all possible model permutations (i.e. 8–64 models) of the explanatory variables. Each one of the five variable categories was first modelled independently for each landscape resolution. The models obtained for each scale and category were ranked using the corrected Akaike's Information Criterion (AICc) and the Akaike weight of each model (ωm), estimated according to Burnham & Anderson (Reference Burnham and Anderson2002). We constructed a 95% confidence set of models by starting with the highest Akaike weight and adding the model with the next highest weight until the cumulative sum of the weights exceeded 0.95 (Burnham & Anderson, Reference Burnham and Anderson2002). A model-filtering procedure was then applied according to Richards (Reference Richards2008). We obtained the best models for each scale, as well as for each category and resolution at the landscape scale. The explanatory variables from the best models (95%) at nest and cliff scale were combined to obtain the best nest-site models by following the same procedure described above. Likewise, at the landscape scale, the explanatory variables from the best models in each category were combined to obtain the best core area and home range models (resolution-specific models).
Finally, the explanatory variables at the nest-site scale were combined with those obtained from each landscape resolution, yielding three final combined models. This procedure allowed us to determine which scale or scale combination best explained the occurrence of the Egyptian vulture by comparing AICc values and the explained deviance of the models. We performed a model averaging approach. Unconditional coefficients for each variable were estimated from all combined models within 95% probability, weighted by ωi (Burnham & Anderson, Reference Burnham and Anderson2002), and resulting in averaged combined models. To ascertain the relative contribution of each variable in the averaged combined models we calculated their Akaike weight (Burnham & Anderson, Reference Burnham and Anderson2002). The variables with the highest weight (Σωi) were more important relative to the others. A hierarchical partitioning analysis was also performed to determine the independent and joint contribution of each variable to the total explanatory power of the model (MacNally, Reference MacNally2002). Interactions of variables included in the final models were also assessed.
From highly inter-correlated variable pairs (Spearman correlation coefficient, |rs| > 0.5), we selected those variables with both the highest independent contribution to the response variable according to a hierarchical partitioning procedure and the highest deviance according to univariate GLMs performed for each explanatory variable. Models were not overdispersed (Lindsey, Reference Lindsey1999). Spatial correlation was assessed in the response variables and residuals of the complete models by inspection of a semivariogram function (gamma; Olea, Reference Olea2009).
Although model evaluation should involve a comparison with independent data, in studies involving rare species and small extents such a dataset is not always available (Gibson et al., Reference Gibson, Wilson, Cahill and Hill2004), as was the case here. The discrimination ability of each complete model was assessed using the area under the receiver operating characteristic curve (Pearce & Ferrier, Reference Pearce and Ferrier2000). Although there are drawbacks to this method an alternative is to use the area under the receiver operating characteristic curve together with specificity and sensitivity when comparing models for the same species in the same area (Lobo et al., Reference Lobo, Jiménez-Valverde and Real2008). The correct classification rate (r = number of sites correctly classified/total number of sites) was also calculated. The thresholds above which the species was considered to be present were established by maximizing the sum of sensitivity and specificity (Liu et al., Reference Liu, Berry, Dawson and Pearson2005). All the analyses were performed with R v. 2.7.2 (R Development Core Team, 2008).
Results
At the nest scale no models were better than the null model (i.e. with intercept only; Appendix 1). At the cliff scale, the best models showed that the probability of abandoning a territory increased on narrower cliffs at high elevation. The best models at the landscape scale demonstrated the positive influence of livestock on territory persistence at all the resolutions considered. The abundance of rocky cliffs also had a strong positive influence on territory permanence. The probability of territory abandonment decreased with high landscape heterogeneity at a 1-km radius and low topographic irregularity at a 2.5-km radius.
The combination of the most important variables at nest, cliff and landscape scales yielded combined models that were much better than resolution-specific models with regard to both deviance and AIC (Table 2; Appendix 2). The best results were obtained at a 2.5-km radius, with the best combined model (ωm = 0.85) explaining 83.97% of deviance (Table 2).
Table 2 Corrected Akaike's Information Criterion (AICc), percentage of deviance explained, percentage of correctly classified cases and discrimination ability (i.e. area under the curve) of the best (Σωm = 0.95) combined and resolution-specific models at the three landscape resolutions (1-, 2.5- and 5-km radii, see text for details).
The three averaged combined models included cliff length and elevation together with livestock, landscape heterogeneity and topography-related variables (Table 3). Landscape heterogeneity favoured territorial persistence at core-area resolution. Livestock was the most important factor influencing territorial persistence at 1- and 5-km radii (Fig. 3). The abundance of cows and sheep at 2.5 km was significant for territory maintenance. The probability of territory abandonment at a 2.5-km resolution decreased with both increasing numbers of cliffs and decreasing slope. Rocky surface was a predictor of Egyptian vulture persistence at 5 km. Because the best 2.5-km combined model had a high weight it was also considered among the best final models (Table 2). The best 2.5-km combined model included the same variables as the 2.5-km averaged combined model, except for cliff length (Table 3).
Fig. 3 Ranking of importance of explanatory variables included in the best averaged combined models that combine nest, cliff and landscape scales with landscape at three resolutions: (a) 1-km radius (core area), (b) 2.5-km and (c) 5-km radii around the nest (see text for details). Variable importance is represented by both the sum of their Akaike weights (Σωi; left) and the percentage of independent and joint contribution to the total explanatory power (hierarchical partitioning analysis; right).
Table 3 Averaged regression coefficients of the explanatory variables (see Table 1 for details) included in the averaged combined models for each landscape resolution (i.e. 1-, 2.5- and 5-km radii, see text for details), and for the best 2.5-km combined model (ωm = 0.85).
No significant effect of spatial autocorrelation was detected in the final averaged combined models. These three models had good discrimination ability, as indicated by the area under the receiver operating characteristic curve and the correct classification rates (Table 2). Overall, the 2.5-km averaged combined model was the best averaging model predicting territory abandonment (proportion of abandoned territories correctly classified ra = 0.86 vs 0.64 and 0.57 for 5-km and 1-km averaged combined models, respectively). Nonetheless, the best 2.5-km combined model was better in predicting territory abandonment (ra = 0.93).
Among the variables included in averaged combined models, livestock was the only one that could have changed significantly during 1997–2007 and hence influenced territory loss. While the cow population increased 22% during 1997–2005, sheep and goats decreased significantly (29%; Fig. 4). The increase in the cow population was larger in abandoned Egyptian vulture territories than in occupied territories (56% vs 16%). However, there were still more cows in occupied than in abandoned territories in 2005 (mean 2,350 ± SE 208 vs 1,922 ± 352). Moreover, during 1997–2005 abandoned territories exhibited a larger decrease in the numbers of sheep and goats than occupied territories (41% vs 26%; χ2 = 806.8, df = 1, P < 0.001; Fig. 4).
Fig. 4 Numbers of livestock in 1997–1999 and 2005–2007 in the municipalities that overlap with the 2.5-km home range of the Egyptian vulture territories occupied and abandoned in the study area. Similar results were obtained for 1- and 5-km resolutions.
Discussion
Factors affecting territory abandonment by the Egyptian vulture
Abandoned territories of the Egyptian vulture were found at high elevations on narrow cliffs in rocky areas with fewer sheep and goats than the occupied territories. Both cliff length and elevation were the only factors from smaller scales selected by the three final averaged combined models (Table 3). Elevation could affect territory quality through weather conditions that, in the study area, are more adverse at higher altitudes. This contrasts with Mediterranean areas, where weather conditions are less adverse and higher elevations are preferred by the species (Liberatori & Penteriani, Reference Liberatori and Penteriani2001). The positive effect of greater cliff length in territory conservation has also been noted in other regions (Liberatori & Penteriani, Reference Liberatori and Penteriani2001). This effect may be related to competition with other cliff-nesters and to presence of predators or occurrence of human disturbance, all of which could be greater on smaller cliffs because of a lower availability of nest sites and greater accessibility for humans and terrestrial predators. In addition, the low availability on narrow cliffs of alternative sites to locate a nest could increase the probability of abandonment. The 1-km averaged combined model retained landscape heterogeneity as a factor positively influencing territory persistence, and landscape heterogeneity has been found to be related to food availability at the national level (Carrete et al., Reference Carrete, Grande, Tella, Sánchez-Zapata, Donázar, Diaz-Delgado and Romo2007). The 2.5-km averaged combined model also retained topographic irregularity, which could make foraging activity difficult and energetically costly (Bergier & Cheylan, Reference Bergier and Cheylan1980).
The positive influence of livestock at all landscape resolutions considered could be explained by its role as a fundamental trophic resource for the Egyptian vulture (Bergier & Cheylan, Reference Bergier and Cheylan1980). As there are no feeding stations in the area, livestock seem to play a key role in the species’ persistence, an association that is largely absent in other regions (Bergier & Cheylan, Reference Bergier and Cheylan1980; Liberatori & Penteriani, Reference Liberatori and Penteriani2001). Although sanitary regulations because of bovine spongiform encephalopathy require the removal of livestock carcasses, these regulations are more relaxed for sheep and goats and in mountain areas with difficult access, as in our study area (Olea & Mateo-Tomás, Reference Olea and Mateo-Tomás2009). The importance of sheep and goats for Egyptian vultures (Sarà & Di Vittorio, Reference Sarà and Di Vittorio2003) was also observed to influence territory persistence in our study area (Fig. 4). While the presence of cows positively influenced territory persistence up to a maximum threshold of 8.9 cows km-2, the probability of territory abandonment steadily decreased when numbers of sheep and goats increased. The greater decrease of sheep and goat populations in abandoned territories (Fig. 4) indicates the role of small livestock in the observed patterns of territory losses.
The incorporation of variables from smaller scales considerably improved the prediction ability of the combined models (Table 2), showing that nest-site scales should also be considered when designing conservation actions for the Egyptian vulture. Our approach allowed us to select the best resolution to predict territory abandonment. Accordingly, the best results were obtained at a 2.5-km radius, corresponding to half the average nearest-neighbour distance in our study area. This stresses the importance of regional analysis to determine reliably the factors driving species extinction. The factors retained by our averaged combined models differ from those favouring territory persistence at the national scale (Carrete et al., Reference Carrete, Grande, Tella, Sánchez-Zapata, Donázar, Diaz-Delgado and Romo2007), underscoring the importance of region-specific management to complement general conservation guidelines (McAlpine et al., Reference McAlpine, Rhodes, Bowen, Lunney, Callaghan, Mitchell and Possingham2008).
Conservation implications
There is an urgent need for the design of an effective management plan for the Egyptian vulture, given the Endangered categorization of the species worldwide (IUCN, 2008). In our study area in the Cantabrian Mountains the importance of small-scale variables indicates the need to control nest sites closely to avoid disturbances that could lead to movement of breeding pairs to suboptimal cliffs, where the probability of abandonment increases. The efficacy of such action has been demonstrated in other areas (Sarà & Di Vittorio, Reference Sarà and Di Vittorio2003). Important human threats such as poison or habitat degradation, which have a detrimental impact in other regions (Carrete et al., Reference Carrete, Grande, Tella, Sánchez-Zapata, Donázar, Diaz-Delgado and Romo2007), do not seem to influence territory abandonment in the Cantabrian Mountains (Table 3). However, the difficulty of obtaining accurate measurements of poisoning (Grande et al., Reference Grande, Serrano, Tavecchia, Carrete, Ceballo and Díaz-Delgado2009) and its delayed effects on populations (Oro et al., Reference Oro, Margalida, Carrete, Heredia and Donazar2008) could hide greater effects.
At the landscape scale conservation measures that promote extensive livestock farming are required in the study area. Although correlational, our study detected an important potential underlying cause of the territory loss (i.e. a strong decrease in the numbers of sheep and goats). The key role that sheep and goats seem to be playing in Egyptian vulture conservation, through maintenance of territories, requires conservation planning specific to this area. The threats derived from changes in livestock can act slowly, compared to others such as poison, but their consequences can be irreversible, profoundly affecting not only the Egyptian vulture but the whole ecosystem. Feeding stations have been frequently recommended in other regions, where researchers have detected a significant influence of livestock on Egyptian vulture conservation (Sarà & Di Vittorio, Reference Sarà and Di Vittorio2003). Although feeding stations are easy to implement they are only partial solutions, with negative long-term consequences for the species and ecosystem (Lemus et al., Reference Lemus, Blanco, Grande, Arroyo, García-Montijano and Martínez2008; Oro et al., Reference Oro, Margalida, Carrete, Heredia and Donazar2008).
The importance, demonstrated by our results, of extensive livestock farming for conservation of the Egyptian vulture is another example of the fundamental role that traditional farming activities can play in ecosystem conservation (Olea & Mateo-Tomás, Reference Olea and Mateo-Tomás2009). Policies are required that allow the maintenance of these low-impact human activities.
Acknowledgements
We thank J.C. del Moral for providing access to the 2nd Spanish Survey of Egyptian Vulture and F. Jubete and J. Placer for providing information about nesting locations. Junta de Castilla y León provided data on poisoning. J. Tomás, J. and J.A. Herrero, M. Gordaliza, F. Carcedo and J. Fernandez provided field assistance. Two anonymous reviewers provided useful comments. PMT was supported by a PhD scholarship of the Spanish Ministerio de Educación y Ciencia. IE University partially funded this study.
Appendix
The appendix for this article is available online at http://journals.cambridge.org
Biographical sketches
Patricia Mateo-Tomás researches the conservation and management of vultures and is currently studying the impacts of traditional human activities on the conservation of biodiversity. Pedro P. Olea carries out conservation biology research with a particular interest in birds. He is currently leading a multidisciplinary team focused on biodiversity conservation, analysing the impact of human activities on ecosystem conservation.
