Research in ecology and conservation biology often relies on long-term population monitoring programs, especially when it focuses on the conservation of long-lived vertebrates (White 2019). However, there are constraints in collecting large volumes of information over long periods. For this reason, observations gathered by citizens, over broad spatial scales and temporal periods, are being used in scientific research allowing studies that would otherwise be unfeasible (Chandler et al. 2012). In particular, photographic records of long-lived species may allow for individual identification on the basis of morphological differences (Marshall and Pierce 2012) and in certain cases, this approach may extend to entire populations (Swanson et al. 2016).
Avian scavengers and Gyps vultures in particular have suffered a precipitous global decline and consequently many of their populations are considered virtually extinct in wide regions of Eurasia and Africa (Prakash et al. 2007, Ogada et al. 2012). In Western Europe, however, Eurasian Griffon Vulture (Gyps fulvus; hereafter Griffon Vulture) populations are still abundant and recovering (see Focal species - Methods). Griffon Vultures are almost entirely dependent on trophic resources provided by human activities such as farming and game hunting (Margalida and Colomer 2012, Monsarrat et al. 2013). As a result, many populations were negatively affected in the late 1990s by the prohibition of livestock carcass abandonment, following the emergence of BSE (Bovine Spongiform Encephalopathy) (Donázar et al. 2010, Cortés-Avizanda et al. 2016). Subsequent European regulations (322/2003/EC, 830/2005/EC, 142/2011/EC) have relaxed this scenario, increasing the availability of carrion from livestock husbandry (Margalida et al. 2012, Arrondo et al. 2018). However, how these changes have affected the demography of avian scavengers remains largely unknown, with the exception of approaches related to breeding parameters and fledgling condition (Margalida and Colomer 2012, Donázar et al. 2020a). This is due to the difficulty in collecting long-term data on a group of birds characterized by conservative life-history traits such as low productivity, delayed sexual maturity, and high longevity.
We used photographs captured by nature photographers and information collected from long-term monitoring of carcass consumption, to examine if the aforementioned changes in sanitary regulations shaped the age structure of Griffon Vultures at different food sources. It has recently been described that immature avian scavengers feed with greater success when resources are more predictable (van Overveld et al. 2018), probably because competition with dominant adults may be higher at randomly distributed sources (Donázar et al. 1999, Moreno-Opo et al. 2020). Additionally, immatures are not spatially attached to breeding areas and frequently perform exploratory displacements (Bamford et al. 2007, Margalida et al. 2013), so they may concentrate at more predictable food sources. Accordingly, we predict that the ratio of immatures to adults at carcasses would be lower in scenarios of reduced food availability, when restrictive sanitary regulations were in force, and would increase as the predictability of the resource is higher.
The Griffon Vulture is present across arid and semi-arid areas of Europe, Asia, and North Africa (Cramp and Simmons 1980). Formerly well distributed and abundant, the species has suffered a severe decline disappearing from large portions of its original distribution. Currently, the Iberian Peninsula holds 95% of the European population with around 34,000 breeding pairs (Margalida et al. 2010, Del Moral and Molina 2018). Griffons have a slow reproductive rate, reaching sexual maturity at 4 calendar years (hereafter c-y, 4 years old) (Blanco et al. 1997). They breed colonially on cliffs and forage over open areas, searching for wild and domestic ungulate carcasses (Martin-Díaz et al. 2020), and usually gather at other food sources, such as landfills and supplementary feeding stations (Cortés-Avizanda et al. 2010, 2012, Monsarrat et al. 2013, Moreno-Opo et al. 2015b).
Our study was performed in the upper Ebro valley, an area covering around 10,000 km2 in northern Spain (Cortés-Avizanda et al. 2012, Fig. 1). This is a lowland region with large extensive cereal cultures and intensive irrigation (Lecina et al. 2005). It is considered one of the most important European regions for avian scavengers (Bijleveld 1974, Cortés-Avizanda et al. 2015, Sanz-Aguilar et al. 2017). During the summer season (April-August) of 2004-2006, we monitored the consumption of 58 experimentally placed carcasses of sheep (Ovis aries) and pigs (Sus scrofa), the main food sources of avian scavengers in the study area. At each carcass, we surveyed every ten minutes recording the number of griffons of each age class (see details in Cortés-Avizanda et al. 2012). Additionally, we analyzed photographs of feeding Griffon Vultures collected by 15 nature photographers from 2008 to 2019. From each monitored or photographed carcass, we selected the single survey or photograph (hereafter feeding event); which had the largest number of individuals of known age. Accordingly, we selected 110 direct observations and 170 photographs. All data were collected with telescopes (20-60x) and at a distance (>200m) or, alternatively, from hides, to avoid interfering with birds’ behavior. We considered two age categories: Immature individuals ranging in age from 1 to 5 c-y and Adults: >5cy. These categories correspond respectively to birds with age equal to, or older than, 5 years. Following Forsman 2003 and Zuberogoitia et al. 2013, we considered as immatures all those birds presenting totally brown neck ruff feathers, as well as dark bills. To avoid possible biases, all age categories from both field observations and photographs were determined by the same observers (i.e., ACA, JAD).
We fit a GLM where the response variable was the ratio of immatures in the group of Griffon Vultures of known age for each feeding event (binomial distribution for proportional data; logit link function). We applied a cbind procedure to the response variable (see Zuur et al. 2009) to account for the effect of different sample sizes (total number of vultures in the observation and/or photograph). Explanatory variables included:
We also considered one interaction with biological significance and a clear predicted effect: Legislation*Resource in order to evaluate the resource-specific influence that may result from long-term changes in sanitary regulations. See Table A1.1 for further details on number of observations in relation to explanatory variables.
We used the dredge function from the MuMIn package (Barton 2019), the stats package for the confidence intervals and the lme4 package for the GLM analysis (Bates et al. 2015). Model selection was made following the Akaike Information Criterion corrected for small sample sizes (AICc, Sugiura 1978). All analyses were performed in RStudio-3.6.0 (RStudioTeam 2018).
We identified a total of 7,413 individual records of known age, 2,953 immatures and 4,460 adults. Modeling procedures revealed that a single model accounts for the total weight with the second model being 34 AICc points below (Table A2.1). The top model (Table 1, Fig. 2) showed that the proportion of immature vultures was higher during summer and in all kinds of resources. Additionally, during the tolerance scenario, there were relatively fewer immatures at both random carcasses and predictable feeding sites. However, the proportion of immatures at landfills remained similar or increased slightly between the two periods.
Photographers’ records are increasing the availability of information in fields where conventional research is progressing slowly, thus enabling robust analyses with large amounts of data. We used information collected through both, scientific research (39% of data) and from photographs captured by naturalists (61%), to demonstrate the existence of long-term changes in the age structure of a vulture population under a scenario of adjusted food resources driven by sanitary regulations. Thus, we recorded that the proportion of immatures at landfills and predictable feeding sites became significantly higher than at random carcasses during the tolerance legislation scenario.
We are confident that our results are not biased in methodological procedures. Although visual censuses register more individual records than can be counted in a photograph, there is no reason to believe that this affected the age structure but simply the number of birds recorded in a single event, which, in turn, is controlled in the analyses. Also, we do not believe that photographers biased their photos towards a single age group nor there is reason to believe that different species of livestock carcass (pigs or sheep) are exploited by different age categories (Moreno-Opo et al. 2015a). We know that environmental conditions, not the ungulate species scavenged, determine the interspecific composition of scavenger guilds (Arrondo et al. 2019), and there is no reason to believe that the guild´s composition differs at the intraspecific level.
The first result, showing a higher proportion of immature birds in summer was expected. It is known that immature Griffon Vultures perform short migrations and nomadic displacements mainly during winter (Bernis 1983, Griesinger 1998, Ramírez 2018). More interesting was that, in the years of the Tolerance legislation scenario (from 2014 onwards), with more available food, the proportion of immature vultures decreased at random carcasses and, to a lesser extent in predictable feeding sites. In other words, new food sources in the form of random carcasses (available after farmers were permitted to abandon the remains of livestock) would be exploited preferably by adult birds. Conversely, immature birds still tend to concentrate in landfills. It is well established that immature raptors use different foraging strategies relative to adults, tending to congregate in areas where resources are more abundant, predictable, and clumped (Hiraldo et al. 1995, Carrete et al. 2006, van Overveld et al. 2018). Nevertheless, alternative explanations do exist. The population from our study area, in keeping with the rest of the Iberian Peninsula, had grown by 63% in the previous ten years (Del Moral and Molina 2018). Therefore, the increase in the number of immatures could also be a natural occurrence determined by this population growth. Nevertheless, even within this hypothetical scenario, the survival rate of the immature proportion of the population would be required to have increased, but there is no demographical evidence supporting this. Of note, from 1990 to 2005, multiple poisoning events occurred in Spain, resulting in the deaths of up to 16,820 Griffon Vultures (WWF/Adena 2008). No information is currently available to discern whether this unnatural mortality event might have differentially affected particular age demographics, a phenomenon that has been demonstrated among other bird species (e.g., Greater flamingo, Phoenicopterus roseus, Egyptian vulture, Neophron percnopterus) (Tavecchia et al. 2001, Sanz-Aguilar et al. 2017).
The maintenance or slight increase of the proportion of immatures at landfills during the whole study period is remarkable. Landfills, although considered to be lower-quality food sources, are frequently visited by obligate and facultative scavengers (Oro et al. 2008, Tauler et al. 2015, McGrady et al. 2018). We propose different explanations for this finding. Firstly, landfills may act as extremely predictable food sources where non-breeding individuals can feed successfully, with less direct competition with adults. This is a phenomenon that has been reported in many avian species including gulls, other diurnal raptors, and other scavengers (Donázar 1992, Skórka and Wójcik 2008, Turrin et al. 2015). Secondly, it is possible that the availability of livestock carcasses has not increased dramatically despite the introduction of less severe sanitary regulations. This may be a result of relatively few livestock farmers availing of the opportunities provided by the legislation or, more importantly, the large-scale decline of extensive farming practices (Pereira and Navarro 2015). Furthermore, the larger aggregations of immatures found at landfills could be in response to a possible specialization on a certain type of resource (in our case random carcasses) with age (Araújo et al. 2011, Sanz-Aguilar et al. 2015), and/or to an increase in the intra-specific competition at random resources, linked to the abandonment of traditional farming practices and land uses (Cortés-Avizanda et al. 2015). Such scenarios may lead to the displacement of immatures to less profitable and lower-quality food sources, which ultimately may lead to death caused by malnutrition, higher chances of contracting diseases, or the ingestion of toxins or pathogens (Plaza and Lambertucci 2018, Blanco et al. 2019). Additionally, landfills, which are generally placed in highly anthropogenic areas may also induce higher risk of non-natural mortality (Arrondo et al. 2020). This may act as an ‘ecological trap’ (Begon et al. 2006), potentially reducing the survival rates of non-breeding birds which can ultimately affect population viability of the remaining European population of Griffon Vultures (Oro et al. 2013).
Our results revealed that the age structure of a focal top-scavenger population responded to changes in the availability and predictability of trophic resources mediated by sanitary regulations. In particular, we show age-specific resource exploitation patterns, with adult birds profiting more from more randomly distributed resources and immatures depending on low-quality feeding sites such as landfills. To disentangle the contribution of these factors is not banal since it is well-known that populations of endangered species are sensitive to modifications of food subsidies (Gouar et al. 2008, Oro et al. 2008, Margalida and Colomer 2012). The management of predictable resources has been considered a tool in the recovery of endangered vulture populations (Cortés-Avizanda et al. 2016, Tauler-Ametller et al. 2017), but here we show that this can have hidden consequences. Further research is required to achieve a better understanding of how food subsidization and anthropization affect the scavenging guild, the associated ecosystem, and the services it provides for society.
Conceived and designed the study: ACA and JAD. Fieldwork: ACA and JAD. Designed the methodology: LFG ACA and JAD. Compiled the data, prepared data and performed analyses: LFG, ACA and FB. LFG, ACA, PT and JAD led the writing of the manuscript. All authors contributed critically to the drafts and gave final approval for publication.
Photographs were kindly provided by J. Ardaiz, L. Goñi, J.M. Lekuona, D. García, R. Rodríguez, M. de la Riva, D. Serrano, E. Blanco, S. González, L. Rivas, J.J. Vega, J.M. Martínez, I. Arrospide, A. Senosiain, and J.A. Pinzolas. ACA was supported by a post-doctoral contract of Excellence project of Junta de Andalucía and a post-doctoral contract EMERGIA of Junta de Andalucía. This work was partially funded by the Project RTI2018-099609-B-C21 (Spanish Ministry of Economy and Competitiveness and EU/FEDER) and AAEE123/2017.
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