Hostname: page-component-848d4c4894-xfwgj Total loading time: 0 Render date: 2024-06-19T19:48:49.491Z Has data issue: false hasContentIssue false
  • English
  • Français

Habitat features of settlement areas used by floaters of Bonelli’s and Golden Eagles

Published online by Cambridge University Press:  23 April 2010

JESÚS CARO ,
DIEGO ONTIVEROS ,
MANUEL PIZARRO  and
JUAN M. PLEGUEZUELOS
JESÚS CARO*
Affiliation:
Departamento de Biología Animal, Facultad de Ciencias, Universidad de Granada, E-18071, Granada, Spain.
DIEGO ONTIVEROS
Affiliation:
Departamento de Biología Animal, Facultad de Ciencias, Universidad de Granada, E-18071, Granada, Spain.
MANUEL PIZARRO
Affiliation:
Departamento de Biología Animal, Facultad de Ciencias, Universidad de Granada, E-18071, Granada, Spain.
JUAN M. PLEGUEZUELOS
Affiliation:
Departamento de Biología Animal, Facultad de Ciencias, Universidad de Granada, E-18071, Granada, Spain.
*
*Author for correspondence; e-mail: jcaro@ugr.es.
Rights & Permissions [Opens in a new window]

Summary

Bonelli’s Eagle Hieraaetus fasciatus and Golden Eagle Aquila chrysaetos are two declining species, in which floaters tend to be located outside of breeding territories during the dispersal period, in so-called settlement areas. We studied settlement areas for both these long-lived raptors in the southern Iberian Peninsula, to gain a better understanding of the ecological requirements of the eagles during their long pre-adult stage, a period accounting for around 80% of the species’ mortality. Eagle abundance was calculated by road censuses, and habitat characteristics of settlement and non-settlement areas compared by General Discriminant Analysis (GDA) and Logistic Regression (LR). The best model of GDA and LR incorporated the abundance of main prey for eagles (rabbits, partridges) and orchard surface area, and explained 100% of eagle presence; the best model selected by GDA also included habitat heterogeneity. Both eagles tended to share settlement areas in the southern Iberian Peninsula and, when they did not, the mean annual temperature and slope appeared to explain the segregation between the two species. Management measures for the conservation of both threatened species during the dispersal period should be focused on identifying settlement areas, maintaining high prey densities and maximum habitat heterogeneity.

Resumen

El Águila Perdicera Hieraaetus fasciatus y el Águila Real Aquila chrysaetos son dos especies en declive, cuyos inmaduros tienden a localizarse fuera de los territorios de los reproductores durante el período de dispersión, en zonas conocidas como áreas de asentamiento. Hemos estudiado estas áreas para ambas rapaces en el sur de la Península Ibérica, con el fin de comprender mejor las necesidades ecológicas durante su prolongada etapa preadulta, un periodo en el que en torno al 80% de los individuos mueren. Mediante censos en carriles se calculó la abundancia de las dos águilas, y se midieron las características del hábitat en áreas de asentamiento y no asentamiento comparándose mediante un Análisis Discriminante General (ADG) y una Regresión Logística (RL). El mejor modelo del ADG y RL incluye la abundancia de las presas principales de las águilas (conejos, perdices) y el porcentaje de cultivos arbóreos, explicando el 100% de la presencia de las águilas, y el mejor modelo seleccionado por el ADG también incluyó la heterogeneidad de hábitats. Ambas águilas tendieron a compartir las zonas de asentamiento en el sur de la Península Ibérica y, cuando esto no ocurrió, la temperatura media anual y la pendiente parecían explicar la segregación entre las dos especies. Las medidas de gestión para la conservación de ambas especies amenazadas durante el periodo de dispersión deben centrarse en la identificación de las áreas de asentamiento, el mantenimiento de altas densidades de presas y de alta heterogeneidad de hábitats en estas áreas.

Type
Research Articles
Information
Bird Conservation International , Volume 21 , Issue 1 , March 2011 , pp. 59 - 71
Copyright
Copyright © BirdLife International 2010

Introduction

From an ecological perspective, dispersal affects species distribution and abundance, population dynamics and persistence, and community structure (Dieckmann et al. Reference Dieckmann, O′Hara and Weisser1999). Within a biogeographical context, dispersal is not only important for geographical spread, but also seems to have genetic consequences (e.g. inbreeding reduction and gene exchange between populations; Janes Reference Janes and Cody1985). Often during the dispersal period, floater individuals of some long-lived raptors, such as Bonelli’s Eagle Hieraaetus fasciatus and Golden Eagle Aquila chrysaetos, tend to stay in settlement areas outside of breeding territories where they remain for a variable period before joining breeding populations (Ferrer Reference Ferrer1993, Mañosa et al. Reference Mañosa, Real and Codina1998). The dispersal period is relatively long and critical for these raptors (Newton Reference Newton1979, Watson Reference Watson1997, Mañosa et al. Reference Mañosa, Real and Codina1998), as it accounts for approximately 80% of floater mortality among large raptor species in Mediterranean areas (Real et al. Reference Real, Grande, Mañosa and Sánchez-Zapata2001, Díaz Reference Díaz2004, Carrete et al. Reference Carrete, Sánchez-Zapata, Calvo and Lande2005). The factors affecting survival during the non-breeding stage have major consequences for population stability in these species (Arroyo Reference Arroyo, Madroño, González and Atienza2004, Ontiveros et al. Reference Ontiveros, Real, Balbontin, Carrete, Ferrero, Ferrer, Mañosa, Pleguezuelos and Sánchez-Zapata2004, Margalida et al. Reference Moreno, Villafuerte and Delibes2008, Soutullo et al. Reference Soutullo, López-López and Urios2008a).

Bonelli’s Eagle and Golden Eagle are long-lived birds of prey that nest mainly on cliffs and have a modal clutch size of two eggs (range 1–3), with young maturing at about 4–5 years (Cramp and Simmons Reference Cramp and Simmons1980). These raptors could coexist in settlement areas in the southern Iberian Peninsula (Ferrer Reference Ferrer1993), where the lack of appropriate settlement areas or reduction in habitat quality may decrease floater survival and seriously threaten population stability (Mañosa et al. Reference Mañosa, Real and Codina1998, Arroyo Reference Arroyo, Madroño, González and Atienza2004, Ontiveros et al. Reference Ontiveros, Real, Balbontin, Carrete, Ferrero, Ferrer, Mañosa, Pleguezuelos and Sánchez-Zapata2004). In recent decades, Bonelli’s and Golden Eagles have shown a marked decline throughout most of their distribution and thus are currently considered endangered species in Western Europe (BirdLife International/European Bird Census Council 2000, Arroyo Reference Arroyo, Madroño, González and Atienza2004, Real Reference Real, Madroño, González and Atienza2004). Declines have been attributed to habitat change, direct persecution, electrocution by electric power lines, decrease in prey abundance, and disturbance (Watson Reference Watson1997, Arroyo Reference Arroyo, Madroño, González and Atienza2004, Ontiveros et al. Reference Ontiveros, Real, Balbontin, Carrete, Ferrero, Ferrer, Mañosa, Pleguezuelos and Sánchez-Zapata2004). The development of effective conservation programmes for threatened species such as these requires a clear understanding of the factors determining their distribution and abundance as well as their ecological requirements (Soulé and Wilcox Reference Soulé and Wilcox1980).

Until now, most studies on the conservation of raptors have been focussed on their breeding biology, habitat selection, diet composition, survival, and interspecific interactions (e.g. Real et al. Reference Real, Grande, Mañosa and Sánchez-Zapata2001, Borgo Reference Borgo2003, Penteriani et al. Reference Penteriani, Balbontin and Ferrer2003, Ontiveros et al. Reference Ontiveros, Real, Balbontin, Carrete, Ferrero, Ferrer, Mañosa, Pleguezuelos and Sánchez-Zapata2004, Reference Ontiveros, Pleguezuelos and Caro2005, Carrete et al. Reference Carrete, Sánchez-Zapata, Calvo and Lande2005, McIntyre et al. Reference McIntyre, Steenhof, Kochert and Collopy2006, Jenkins et al. in press, Rollan et al. in press). However, detailed reports on habitat selection by these raptor species during the dispersal phase are scarce (Arroyo Reference Arroyo, Madroño, González and Atienza2004, Real Reference Real, Madroño, González and Atienza2004) and as a consequence, this life stage cannot be adequately considered in management strategies. Studies have shown that floaters of Bonelli’s and Golden Eagles may cover large areas during the dispersal phase (Cadahia et al. 2005, Soutullo et al. Reference Soutullo, Urios, Ferrer and Peñarrubia2006), becoming established in settlement areas with high densities of their main prey (Mañosa et al. Reference Mañosa, Real and Codina1998, Balbontín Reference Balbontín2005, Soutullo et al. Reference Soutullo, Urios, Ferrer and López-López2008b).

Here we provide data on some of the most important settlement areas of Bonelli’s Eagle and Golden Eagle in the southern Iberian Peninsula, characterising the habitat selection of dispersing eagles, and we examine the possible sympatry of the two eagles in these settlement areas. The results may help to identify potential settlement areas for floater eagles of both species elsewhere, thus having implications for management strategies for the two species.

Methods

Study area

The study area was located in southern Spain, in two different administrative regions, Andalucía and Murcia, where Bonelli’s and Golden Eagle populations are the most healthy and well known (Gil-Sánchez et al. Reference Gil-Sánchez, Moleón, Otero and Bautista2004, Ontiveros et al. Reference Ontiveros, Pleguezuelos and Caro2005, Carrete et al. Reference Carrete, Sánchez-Zapata, Tella, Gil-Sánchez and Moleón2006), with 294–333 pairs of Bonelli’s Eagle and 256–290 pairs of Golden Eagle (Arroyo Reference Arroyo, Madroño, González and Atienza2004, Real Reference Real, Madroño, González and Atienza2004). The area is largely mountainous, and the climate is typically Mediterranean, with annual temperatures averaging 15.6–19.5 °C and annual rainfall averaging 300–790 mm (CMA 1997, Carrete et al. Reference Carrete, Sánchez-Zapata, Martínez, Sánchez and Calvo2002). The field work covered 12 areas (see below and Figure 1) where natural vegetation consisted of shrubs, grasslands, and mixed forest of Quercus rotundifolia and Pinus spp., but human activity (notably farming) over the millennia has transformed the landscape into a mosaic. These areas suffer much anthropogenic disturbance and are not protected, which may lead to increasing mortality risk for floaters.

Figure 1. Study area showing settlement (solid circles) and non-settlement (empty circles) areas for Bonelli’s and Golden Eagles in Southern Spain. Numbers refer to the number of 9-km2 squares sampled in each area. For details, see the Methods section.

Raptor survey

Based on our field experience during the last 18 years and the literature (Real Reference Arroyo, Madroño, González and Atienza2004, Balbontín Reference Balbontín2005), we located six settlement areas in the study area. For comparative purposes, we selected six non-settlement areas in the region among those that matched the following characteristics: located outside breeding territories (at least 5 km from closest nest), far away from urban areas (at least 5 km from the central point), below 1,700 m asl (maximum altitude of hunting areas for Bonelli’s Eagle, and for most of the Golden Eagles in the study area), and with no record of floater eagles prior to this study (from the authors’ data). We surveyed the 12 different areas during 2001–2006. Firstly, sampling was performed in autumn and winter, seasons when maximum density can be attained for floater eagles in settlement areas (Mañosa et al. Reference Mañosa, Real and Codina1998, authors’ unpubl. data), to confirm presence/absence of floaters in settlement/non-settlement areas, respectively. Afterwards, areas with floater presence were sampled on a monthly basis while non-settlement areas were sampled more irregularly.

Eagle presence and density were determined by driving along line transects, at a slow speed (20 km hr−1), in as straight a line as possible, on days of good visibility, in the morning, with two people (one trained observer and a driver). This method has repeatedly proved adequate to gather information on the distribution and relative abundance of raptors (Mañosa et al. Reference Mañosa, Real and Codina1998, Sánchez-Zapata and Calvo Reference Sánchez-Zapata and Calvo1999; see discussion by Carrete et al. Reference Carrete, Tella, Blanco and Bertellotti2009). In total, 75 transects were sampled in the six settlement areas, and 20 in the six non-settlement areas, with a total of 1,543 km of line transects covered. The number of kilometres driven and number of individuals of each raptor species were recorded, and eagles were classified as juvenile (1 year), immature, (2–3 years for Bonelli’s Eagle and 2–4 years for Golden Eagle), subadult (4 years for Bonelli’s Eagle and 5 years for Golden Eagle), and adult (> 4 years for Bonelli’s Eagle and > 5 years for Golden Eagle), according to plumage criteria (Parellada Reference Parellada1984, Watson Reference Watson1997, Forsman Reference Forsman1999). Relative abundance of floater eagles in each survey was measured as the average number of birds detected per 100 km.

Habitat selection variables

Each area (both settlement and non-settlement) was divided into 3 × 3 km squares (UTM grid system), and according to the extent of the rather homogeneous landscape in the area, between two and four squares were selected. In total, we selected 29 squares, 16 with presence (for the six settlement areas) and 13 with absence of Bonelli’s and Golden Eagles (for the six non-settlement areas; Figure 1).

Landscape characteristics for each 3 × 3 km square in settlement and non-settlement areas were analysed by means of a Geographic Information System (GIS). Squares 3 × 3 km (900 ha) constitute an appropriate scale for habitat-selection studies in raptors (Mañosa et al. Reference Mañosa, Real and Codina1998, Sánchez-Zapata and Calvo Reference Sánchez-Zapata and Calvo1999, Balbontín Reference Balbontín2005, López-López et al. Reference López-López, García-Ripollés, Aguilar, García-López and Verdejo2006). We measured different variables (Table 1) and related them to the presence or absence of floater eagles in the dispersal phase. Topography, climate, and human population density variables were taken from Corine Land Cover (1:25,000; CEC 1991). Land use variables (habitat heterogeneity, percentage of orchards, pastureland, scrubland, and forest) were taken from soil-use maps of the regions of Andalucía and Murcia (CMA 1999, CAAMA 2000). The number of kilometres of paved and unpaved roads and the distance to the nearest nest of Bonelli’s or Golden Eagle were measured from 1:50,000 digital military maps using Arc View GIS 3.2. We controlled for spatial autocorrelation by including as covariates the geographic variables longitude (Long) and latitude (Lat) of the centre of the squares, as well as the terms Long2, Long3, Lat2, Lat3, Long2 × Lat, and Long × Lat2, according to Legendre (Reference Legendre1993). To compare the presence of the two eagle species, we also used abundance of Bonelli’s and Golden Eagles in breeding territories, computed as the frequency of UTM 10 × 10 km squares with eagle presence into UTM 50 × 50 km squares (Martí and Del Moral Reference Martí and Del Moral2003). Any significant change in land use was noted in the study area during the study period.

Table 1. Variables used (except geographical ones), their values, and comparison (Student’s t- test) between settlement and non-settlement areas of large diurnal raptors (Bonelli’s and Golden Eagles) in southern Spain. Sampling unit was 3 × 3 km square (UTM grid system). More information in the Methods section. Asterisks indicate significance after Bonferroni sequential correction.

Furthermore, we recorded the abundance of the main prey of the Bonelli’s and Golden Eagles in each 3 × 3 km square. In the study area, European Rabbits Oryctolagus cuniculus, Red-legged Partridges Alectoris rufa and pigeons (Columba palumbus and C. livia) account for 79.2% and 61.9%, respectively, of the dietary biomass of these eagles (Delibes et al. Reference Delibes, Calderón and Hiraldo1975, Gil-Sánchez et al. Reference Gil-Sánchez, Molino and Valenzuela1994, Ontiveros et al. Reference Ontiveros, Pleguezuelos and Caro2005). Line transects were used to provide an index of prey density in each square in the settlement and non-settlement areas. This method has proven effective in determining prey abundance for raptors and in comparing prey densities among different zones (Fitzner et al. Reference Fitzner, Rogers and Uresk1977), being less difficult to perform than absolute-density methods and equally useful (Caughley Reference Caughley1977). Prey density was measured as the mean number of individuals per kilometre of census. On average, 4 km of census per year were carried out in each square, stratified according to the surface area of the habitats (Caughley Reference Caughley1977), for two consecutive years (2005 and 2006). Censuses were made by one observer on foot, 06h00–09h30, on days of good visibility, at a speed of approx. 2 km h−1, during the same period (February–April) for all areas. We did not undertake censuses before February so as to avoid the hunting season, and after April because of demographic explosions of rabbits in the southern Iberian Peninsula (Soriguer Reference Soriguer1981). The line transect is the most accurate method for estimating rabbit abundance (Palomares Reference Palomares2001), and diurnal censuses proved to be useful for this species (Soriguer et al. Reference Soriguer, Pérez and Fandos1997, Serrano Reference Serrano1998, Palomares et al. Reference Palomares, Delibes, Revilla, Calzada and Fedriani2001), since rabbits, although primarily nocturnal, also show substantial diurnal activity (Soriguer and Rogers Reference Soriguer and Rogers1981, Moreno et al. Reference Moreno, Villafuerte and Delibes1996); thus, we deemed the diurnal rabbit census to be a more realistic estimate of prey density for strictly diurnal predators such as Bonelli’s and Golden Eagles (Ontiveros et al. Reference Ontiveros, Pleguezuelos and Caro2005).

Statistical procedures

Non-parametric variables were log-transformed (Sokal and Rohlf Reference Sokal and Rohlf1995), and we performed the statistical analysis in three steps:

  1. i) We used the Student’s t-test to identify differences in the variables between settlement and non-settlement squares for floater eagles, and with Bonelli’s Eagle presence vs. Golden Eagle presence, and included squares with presence of both species once in each group. A circular statistic was used for analyses of orientation in settlement areas (Rayleigh’s test), since a simple arithmetic mean of recorded angles is inadequate (Fisher Reference Fisher1995).

  2. ii) We used a General Discriminant Analysis (GDA) to identify the variables that explained differences between areas with presence or absence of floater eagles. These analyses allowed models to be generated by stepwise selection of predictors as well as by the selections of the best-subset of predictors. We chose the latter approach, which allows model uncertainty to be measured at the same time as parameter uncertainty, to assess the likely bias in parameters resulting from selections. We used Statistica 7.0 software, which may generate multivariate linear models, and ranks the set of all possible models by their Wilks’s lambda values (an estimate of the unexplained variance), separately within each model order (k = 1, 2, … 14), where a model’s order is defined as the number of predictor variables it includes. We retained the five best subset models from orders 1, 2, …13, and also the single model containing all 14 predictors, for a total of 66 candidate models. Smaller values indicate a better, more parsimonious model and denote strong group separation (Quinn and Keough Reference Quinn and Keough2003). From all possible models generated in the analysis, we chose those explaining the highest percentage of presence-absence of the eagles with fewer variables. Because in our analysis the sample size could not be increased to three times the number of variables measured, a jack-knife classification was carried out for the analysis (Willians and Titus Reference Willians and Titus1988).

  3. iii) We used logistic regression (LR) (Siegel and Castellan Reference Siegel and Castellan1988, Jongman et al. Reference Jongman, Ter Braak and van Tongeren1995), to explore their coincidence with previous results from the GDA. Logistic regression is often applied to ornithological data for predicting presence or absence of species (Fielding and Bell Reference Fielding and Bell1997, Manel et al. Reference Manel, Dias, Buckton and Ormerod1999). To eliminate variables without significant effects on the presence of the eagles, we performed a forward stepwise model.

Results

In the settlement areas, we recorded 41 observations of Bonelli’s Eagles and 29 of Golden Eagles, with 2.27 ± 2.98 eagles 100 km−1 (mean ± standard deviation) and 2.31 ± 1.89 eagles 100 km−1 for Bonelli’s Eagle and Golden Eagle, respectively. The age ratio of the eagles was 73.17% and 58.62% juvenile, 17.07% and 31.04% immature, and 9.76% and 10.34% subadult individuals of Bonelli’s and Golden Eagles, respectively, as we did not observe any adult eagles during the censuses. No significant interspecific difference was found in the abundance index in settlement areas (Mann-Whitney U-test, Z = -0.322, P = 0.74, n = 6) and the age frequency (Kolmogorov-Smirnov test, Dmax = 0.25, P > 0.1, n = 4).

Overall, 16 3 × 3 km squares in six different settlement areas and 13 3 × 3 km squares in six non-settlement areas (Figure 1) were used to compare settlement preferences for floater Bonelli’s and/or Golden Eagles. In those settlement areas, we observed the presence of only Bonelli’s Eagle in four 3 × 3 km squares and only Golden Eagle presence in seven squares, while both eagles were observed in the remaining five squares. Squares with floater eagles differed significantly from those without floater eagles in terms of abundance of European Rabbits, Red-legged Partridges, and presence of orchards, which were all greater in settlement areas (Table 2). These differences remained significant after Bonferroni correction. No significant interannual difference was found in any prey density in any of the areas surveyed (Kruskal-Wallis test: H1,8 < 1.33, P > 0.25, in all cases). The mean orientation and angular deviation of slopes in squares with presence and absence of floater eagles were 237.96° ± 54.43° and 345.99° ± 54.99°, respectively. Squares with the presence of floater eagles revealed a trend towards a south-western orientation (Raleigh test = 0.35, P = 0.007).

Table 2. Mean, standard deviation (SD), and comparison (Student’s t-test) for variables in settlement areas with presence of Bonelli’s and Golden Eagles in southern Spain.

In the GDA differentiating settlement and non-settlement areas, 66 best-subset models were generated. Wilks’s lambda values consistently stabilised after four variables. The differential score between the lowest Wilks’s lambda and the best model with four variables was only 0.062. The abundance of European Rabbits and Red-legged Partridges, the percentage of orchards, and the habitat heterogeneity, were considered the best predictors of presence or absence of floater eagles (Wilks’s lambda = 0.162, F(4,24) = 30.996, P < 0.001). The best models were (see Table 1 for the meaning of the variable acronyms):

Square with eagle presence=−10.15 − 0.97 IKAORYC + 0.27 IKAALEC + 0.01 ORCH + 2.28 HETERO

Square with eagle absence=−22.72 − 3.15 IKAORYC − 0.49 IKAALEC − 0.19 ORCH + 3.44 HETERO

With these equations, 100% of the squares with presence or absence of floater eagles were correctly classified. A jack-knife classification reduced the correct classification of presence to 99.3% and of absence to 95.9%.

The best LR model for the identification of settlement areas coincided with the GDA in three out of the four variables, also setting abundance of European Rabbit, Red-legged Partridge, and percentage of orchards, as the most parsimonious predictors (χ23=39.645, P<0.001). The best model was:

This model also classified correctly 100% of the squares, thus the inclusion of other variables did not improve the final model.

The best model of GDA and LR did not include any spatial variable, suggesting that there was no effect of spatial autocorrelation. Squares with Bonelli’s Eagle exhibited higher average annual temperature and slope than those with the Golden Eagle (Table 2), although the differences became non-significant after Bonferroni correction.

Discussion

All statistical analyses showed that settlement areas selected by floater eagles had a greater presence of their main prey and orchards than non-settlement areas; the best model selected by GDA also included habitat heterogeneity, defined as the number of different land use types in each square (see Atauri and de Lucio Reference Atauri and de Lucio2001). Furthermore, discriminant and logistic regression analysis coincided in identifying these variables to explain almost all the variance of the settlement areas, despite variability in landscapes throughout the wide geographic range of the study area. In the study area, orchards consisted mainly of olive trees, and several studies have shown the importance of this traditional landscape as a habitat for rabbits and partridges (Rogers et al. Reference Rogers, Arthur, Soriguer, Thomson and King1994, Vargas et al. Reference Vargas, Guerrero, Farfán, Barbosa and Real2006). Higher habitat heterogeneity also favours the presence of these game species, and landscapes with these characteristics can be considered good foraging habitats for raptors (Sánchez-Zapata and Calvo Reference Sánchez-Zapata and Calvo1999, Fortuna Reference Fortuna2002, Sergio et al. Reference Sergio, Marchesi and Pedrini2004). The statistical analysis of circular data also showed that settlement areas tended towards a south-western orientation. In the morning in the study area, the air warms up and ascends (thermal bubbles) on south-facing slopes, frequently used by raptors to save energy during gliding flight (Janes Reference Janes and Cody1985, Ontiveros Reference Ontiveros1999), especially Bonelli’s Eagle, which has poor flying lift in flat areas (Parellada et al. Reference Parellada, De Juan and Alamany1984). Similarly, Balbontín (Reference Balbontín2005) also found sunny orientations to be selected in the settlement areas of Bonelli’s Eagle in south-western Spain.

Two studies have analysed local settlement areas for floater eagles in the Iberian Peninsula, although only for Bonelli’s Eagle (Mañosa et al. Reference Mañosa, Real and Codina1998, Balbontín Reference Balbontín2005). Coinciding with Mañosa et al. (Reference Mañosa, Real and Codina1998), we found in the present study that settlement areas for both eagle species were selected mainly for food availability rather than for topography or landscape patterns. Contrary to the present study and Mañosa et al. (Reference Mañosa, Real and Codina1998), Balbontín (Reference Balbontín2005) found that the habitat selection of floater Bonelli’s Eagle was related to topography, land use, and human disturbance. However, although this author did not consider prey abundance, the land use variables in his study that were selected by eagles (scrub and pasture) were directly related to a higher presence and/or detectability of the main prey species, such as partridges and rabbits (Fortuna Reference Fortuna2002, Ontiveros et al. Reference Ontiveros, Pleguezuelos and Caro2005). Soutullo et al. (Reference Soutullo, Urios, Ferrer and López-López2008b) found that juvenile Golden Eagles used a wide range of habitats in eastern Spain, at least when yearlings (1–2 years old), though showed some preference for certain types of habitat, such as coniferous forest, sclerophyllous vegetation, and mosaic agricultural landscapes. As in our results, settlement areas of Spanish Imperial Eagle Aquila adalberti in southern Spain were characterised by high rabbit densities and the presence of pasture, farmlands and dehesas (Ferrer Reference Ferrer1993, Ferrer and Harte Reference Ferrer and Harte1997).

In relation to density, Mañosa et al. (Reference Mañosa, Real and Codina1998), reported an encounter rate of 2.7 eagles 100-km−1 in one settlement area of Bonelli’s Eagle in north-eastern Spain, similar to the value found in the present study as an average of six different settlement areas. Likewise, the percentages of juvenile, immature, and subadult individuals were similar to those found in our study.

Our results showed no significant interspecific differences in abundance and age frequency between the two eagle species, rather there was high habitat overlap between species in settlement areas. Only lower mean annual temperatures and the steepest slopes appear to account for the higher presence of Golden Eagle over Bonelli’s Eagle in settlement areas. The segregation mediated by environmental temperature has also been found in breeding populations, related to differences in their niche for that trait (López-López et al. Reference López-López, García-Ripollés, Aguilar, García-López and Verdejo2004, Moreno-Rueda et al. Reference Moreno-Rueda, Pizarro, Ontiveros and Pleguezuelos2009), because Bonelli’s Eagle is more thermophilic than Golden Eagle (Muñoz et al. Reference Muñoz, Real, Barbosa and Vargas2005, López-López et al. Reference López-López, García-Ripollés, Soutullo, Cadahía and Urios2007). It is remarkable that two large raptor species with similar ecological requirements coincided to some degree in the settlement areas considered here, also exhibiting similar values of abundance and age-frequency densities. This coincides with the recent perspective on breeding populations of both eagle species, which suggest that long-term coexistence is likely (López-López et al. Reference López-López, Soutullo, García-Ripollés, Urios, Cadahía and Ferrer2008), intraspecific competition being more important than interspecific for neighbouring pairs (Carrete et al. Reference Carrete, Sánchez-Zapata, Calvo and Lande2005; but see Gil-Sánchez et al. Reference Gil-Sánchez, Moleón, Otero and Bautista2004).

The southern Iberian Peninsula harbours large populations of Bonelli’s and Golden Eagles (Arroyo Reference Arroyo, Madroño, González and Atienza2004, Real Reference Real, Madroño, González and Atienza2004), and both species are mainly cliff-nesting raptors that occupy the most rugged areas. However, settlement areas lack adequate nesting cliffs and are closely surrounded by breeding territories. In settlement areas, floaters wait for the occurrence of breeding opportunities within the reproductive fraction of the population. Probably, young eagles select settlements areas under two cues, areas with sufficient food availability in which they can avoid competition with breeders. However, the major threats for both eagles in such areas include prey decrease, habitat change, and persecution, both direct (shooting) and indirect (poisoning) on private hunting estates (Arroyo Reference Arroyo, Madroño, González and Atienza2004, Real Reference Real, Madroño, González and Atienza2004). At least for Bonelli’s Eagle, floater mortality plays a key role in determining the overall population trend in Iberian Peninsula (Soutullo et al. Reference Soutullo, López-López and Urios2008a), and the same applies to other threatened raptors, such as Spanish Imperial Eagle (Penteriani et al. Reference Penteriani, Otalora, Sergio and Ferrer2005, Reference Penteriani, Otalora and Ferrer2008).

Management implications

Because both Bonelli’s and Golden Eagles spend a significant portion of their life (2–4 years) within settlement areas, the location and protection of such areas for these eagles would lengthen their lifespan by protecting the habitat during the floater stage (Balbontín Reference Balbontín2005). Because settlement areas are unknown or difficult to detect, fewer efforts have so far been devoted to the conservation of these sites than to protecting breeding territories (Penteriani et al. Reference Penteriani, Otalora, Sergio and Ferrer2005). However, management action for the conservation of these species should also be focused at minimising floater mortality in settlement areas (Ontiveros et al. Reference Ontiveros, Real, Balbontin, Carrete, Ferrero, Ferrer, Mañosa, Pleguezuelos and Sánchez-Zapata2004, Real Reference Real, Madroño, González and Atienza2004, Soutullo et al. Reference Soutullo, López-López and Urios2008a). Moreover, in Mediterranean Spain, the protection of such settlement areas would benefit both large raptors of conservation concern.

Due to the high importance of rabbit and partridge abundance in settlement areas, the management of these prey species and their habitats is crucial. These game species sustain a large number of natural predators in the Iberian Peninsula (Valkama et al. Reference Valkama, Korpimäki, Arroyo, Beja, Bretagnolle, Bro, Kenward, Mañosa, Redpath, Thirgood and Viñuela2005, Delibes-Mateos et al. Reference Delibes-Mateos, Redpath, Angulo, Ferreras and Villafuerte2007), but are also important for hunting by humans on private hunting estates (Lucio Reference Lucio, Fuentes, Sánchez and Pajuelo1991, Villafuerte et al. Reference Villafuerte, Viñuela and Blanco1998). All the settlement areas considered in this study are included in hunting estates. For these reasons, vigilance of hunting quotas on these estates is necessary for the maintenance of appropriate prey-species abundance. In this way, authorities could establish agreements with hunters, such as economic compensation for not hunting in some years, or through the purchase and management of these areas. Furthermore, agri-environmental measures that encourage low-intensity farming systems should be implemented in these areas. Finally, the conservation of mosaic habitats should be the basis for increasing land-cover diversity and thereby favouring the abundance of the main prey species of floater eagles in the settlement areas.

Acknowledgements

We thank Pedro Gutierrez for his contribution to the field work. Gregorio Moreno provided helpful suggestions on a previous draft, José Poquet helped with the statistical analyses, and David Nesbitt improved the English. Most of this study was performed without financial support.

References

Arroyo, B. (2004) Águila real, Aquila chrysaetos. Pp 151–153 in Madroño, A., González, C. and Atienza, J. C., eds. Libro Rojo de las aves de España. Madrid, Spain: Dirección General para la Biodiversidad-Seo/BirdLife.Google Scholar
Atauri, J. A. and de Lucio, J. V. (2001) The role of landscape structure in species richness distribution of birds, amphibians, reptiles and lepidopterans in Mediterranean landscapes. Landsc. Ecol. 16: 147–159.CrossRefGoogle Scholar
Balbontín, J. (2005) Identifying suitable habitat for dispersal in Bonelli’s Eagle: An important issue halting its decline in Europe. Biol. Conserv. 126: 74–83.CrossRefGoogle Scholar
BirdLife International/European Bird Census Council (2000) European bird populations: estimates and trends. Cambridge, UK: BirdLife International (BirdLife Conservation Series, no. 10).Google Scholar
Borgo, A. (2003) Ecology of the Golden Eagle Aquila chrysaetos in the Eastern Italian Alps. Avocetta 27: 81–82.Google Scholar
Cadahía, L., Urios, V. and Negro, J. J. (2005) Survival and movements of satellite-tracked Bonelli’s Eagle Hieraaetus fasciatus during their first winter. Ibis 147: 415–419.CrossRefGoogle Scholar
Carrete, M., Tella, J. L., Blanco, G. and Bertellotti, M. (2009) Effects of habitat degradation on the abundance, richness and diversity of raptors across Neotropical biomes. Biol. Conserv. 142: 2002–2011.CrossRefGoogle Scholar
Carrete, M., Sánchez-Zapata, J. A., Calvo, J. F. and Lande, R. (2005) Demography and habitat availability in territorial competing species. Oikos 108: 125–136.CrossRefGoogle Scholar
Carrete, M., Sánchez-Zapata, J. A., Martínez, J. E., Sánchez, M. A. and Calvo, F. (2002) Factors influencing the decline of a Bonelli’s Eagle Hieraaetus fasciatus population in southeastern Spain: demography, habitat or competition? Biodivers. Conserv. 11: 975–985.Google Scholar
Carrete, M., Sánchez-Zapata, J. A., Tella, J. L., Gil-Sánchez, J. M. and Moleón, M. (2006) Components of breeding performance in two competing species: habitat heterogeneity, individual quality and density-dependence. Oikos 112: 680–690.Google Scholar
Caughley, G. (1977) Analysis of vertebrate populations. London, UK: Wiley and Sons.Google Scholar
CAAMA (2000) Mapa digital de suelos de la Región de Murcia. Murcia, Spain: Consejería de Agricultura Agua y Medio Ambiente.Google Scholar
CEC (1991) CORINE land cover. Brussels, Belgium: Commission of the European Communities. ECSC-EEC-EAC.Google Scholar
CMA (1997) La información ambiental de Andalucía. Seville, Spain: Junta de Andalucía.Google Scholar
CMA (1999) Leyenda del mapa de usos y coberturas vegetales del suelo de Andalucía. Seville, Spain: Consejería de Medio Ambiente, Junta de Andalucía.Google Scholar
Cramp, S. and Simmons, K. L. (1980) The birds of the Western Palearctic. Vol. II. Oxford, UK: Oxford University Press.Google Scholar
Delibes, M., Calderón, J. and Hiraldo, F. (1975) Selección de presa y alimentación en España del Águila real (Aquila chrysaetos). Ardeola 21: 285–303.Google Scholar
Delibes-Mateos, M., Redpath, S. M., Angulo, E., Ferreras, P. and Villafuerte, R. (2007) Rabbits as a keystone species in southern Europe. Biol. Conserv: 137: 149–156.CrossRefGoogle Scholar
Díaz, J. (2004) Los avatares de las águilas reales jóvenes. Quercus 223: 16–18.Google Scholar
Dieckmann, U., O′Hara, B. and Weisser, W. (1999) The evolutionary ecology of dispersal. Trends Ecol. Evol. 14: 88–90.CrossRefGoogle Scholar
Ferrer, M. (1993) Juvenile dispersal behaviour and natal philopatry of a long-lived raptor, the Spanish Imperial Eagle Aquila adalberti. Ibis 135: 132–138.Google Scholar
Ferrer, M. and Harte, M. (1997) Habitat selection by immature Spanish Imperial Eagles during the dispersal period. J. Appl. Ecol. 34: 1359–1364.CrossRefGoogle Scholar
Fielding, A. H. and Bell, J. F. (1997) A review methods for the assessment of prediction errors in conservation presence: absence models. Environ. Conserv. 24: 38–49.CrossRefGoogle Scholar
Fisher, N. I. 1995: Statistical analysis of circular data. Cambridge, UK: Cambridge University Press.Google Scholar
Fitzner, R. E., Rogers, L. E. and Uresk, D. W. (1977) Techniques useful for determining raptor prey-species abundance. J. Raptor. Res. 11: 67–71.Google Scholar
Forsman, D. (1999) The raptors of Europe and the Middle East. A handbook of field identification. London, UK: T. and A. D. Poyser.Google Scholar
Fortuna, M. A. (2002) Selección de hábitat de la perdiz roja (Alectoris rufa) en período reproductor en relación con las características del paisaje de un agrosistema de la mancha (España). Ardeola 49: 59–66.Google Scholar
Gil-Sánchez, J. M., Molino, F. and Valenzuela, G. (1994) Parámetros reproductivos y de alimentación del águila real (Aquila chrysaetos) y del águila perdicera (Hieraaetus fasciatus) en la provincia de Granada. Aegypius 12: 47–52.Google Scholar
Gil-Sánchez, J. M., Moleón, M., Otero, M. and Bautista, J. (2004) A 9-year study of successful breeding in a Bonelli’s Eagle population in southern Spain: a basis for conservation. Biol. Conserv. 118: 685–694.CrossRefGoogle Scholar
Janes, S. W. (1985) Habitat selection in raptorial birds. Pp 154–188 in Cody, M. L., ed. Habitat selection in birds. London, UK: Academic Press.Google Scholar
Jenkins, A. R., Smallie, J. J. and Diamond, M. (in press) Avian collisions with power lines: a global review of causes and mitigation with a South African perspective. Bird Conservation International doi:10.1017/S0959270910000122.Google Scholar
Jongman, R. H. G., Ter Braak, C. J. F. and van Tongeren, O. F. R. (1995) Data analysis in community and landscape ecology. 4th edn. Cambridge, UK: Cambridge University Press.CrossRefGoogle Scholar
Legendre, P. (1993) Spatial autocorrelation: trouble or new paradigm? Ecology 74: 1659–1673.CrossRefGoogle Scholar
López-López, P., García-Ripollés, C., Aguilar, J. M., García-López, F. and Verdejo, J. (2004) Patrón de distribución del águila real Aquila chrysaetos y del águila-azor perdicera Hieraaetus fasciatus en la provincia de Castellón. Ardeola 51: 275–283.Google Scholar
López-López, P., García-Ripollés, C., Aguilar, J. M., García-López, F. and Verdejo, J. (2006) Modelling breeding habitat preferences of Bonelli’s Eagle (Hieraaetus fasciatus) in relation to topography, disturbance, climate and land use at different spatial scales. J. Ornithol. 147: 97–106.CrossRefGoogle Scholar
López-López, P., García-Ripollés, C., Soutullo, A., Cadahía, L. and Urios, V. (2007) Identifying potentially suitable nesting habitat for Golden Eagles applied to ‘important bird areas’ design. Anim. Conserv. 10: 208–218.Google Scholar
López-López, P., Soutullo, A., García-Ripollés, C., Urios, V., Cadahía, L. and Ferrer, M. (2008) Markov models of territory occupancy: implications for the management and conservation of competing species. Biodivers. Conserv. 18: 1389–1402.CrossRefGoogle Scholar
Lucio, A. (1991) Ordenación y gestión en caza menor. Pp 219–255 in Fuentes, A., Sánchez, I. and Pajuelo, L., eds. Manual de ordenación y gestión cinegética. Badajoz, Spain: Ifeba.Google Scholar
Manel, S., Dias, J. M., Buckton, S. T. and Ormerod, S. J. (1999) Alternative methods for predicting species distribution: an illustration with Himalayan river birds. J. Appl. Ecol. 36: 734–747.CrossRefGoogle Scholar
Mañosa, S., Real, J. and Codina, J. (1998) Selection of settlement areas by juvenile Bonelli’s Eagle in Catalonia. J. Raptor. Res. 32: 208–214.Google Scholar
Margalida, A., Heredia, R., Razin, M. and Hernández, M. (2008) Sources of variation in mortality of the Bearded Vulture Gypaetus barbatus in Europe. Bird Conserv. Internatn. 18: 1–10.CrossRefGoogle Scholar
Martí, R. and Del Moral, J. C. (2003) Atlas de las aves reproductoras de España. Madrid, Spain: SEO BirdLife.Google Scholar
McIntyre, C., Steenhof, K., Kochert, M. N. and Collopy, M. W. (2006) Characteristics of the landscape surrounding Golden Eagle nest sites in Denali National Park and Preserve, Alaska. J. Raptor. Res. 40: 46–51.Google Scholar
Moreno, S., Villafuerte, R. and Delibes, M. (1996) Cover is safe during the day but dangerous at night: the use of vegetation by European wild rabbits. Can. J. Zool. 74: 1656–1660.Google Scholar
Moreno-Rueda, G., Pizarro, M., Ontiveros, D. and Pleguezuelos, J. M. (2009) The coexistence of the eagles Aquila chrysaetos and Hieraaetus fasciatus increases with low human population density, intermediate temperature, and high prey diversity. Ann. Zool. Fenn. 46: 283–290.CrossRefGoogle Scholar
Muñoz, A. R., Real, R., Barbosa, A. M. and Vargas, J. M. (2005) Modelling the distribution of Bonelli’s Eagle in Spain: implications for conservation planning. Divers. Distrib. 11: 477–486.CrossRefGoogle Scholar
Newton, I. (1979) Population ecology of raptors. Berkhamstead, UK: T. and A. D. Poyser.Google Scholar
Ontiveros, D. (1999) Selection of nest cliff by Bonelli’s Eagle (Hieraaetus fasciatus) in southeastern Spain. J. Raptor. Res. 33: 110–116.Google Scholar
Ontiveros, D., Pleguezuelos, J. M. and Caro, J. (2005) Prey density, prey detectability and food habits: the case of the Bonelli’s Eagle and the conservation measures. Biol. Conserv. 123: 19–25.Google Scholar
Ontiveros, D., Real, J., Balbontin, J., Carrete, M., Ferrero, E., Ferrer, M., Mañosa, S., Pleguezuelos, J. M. and Sánchez-Zapata, J. A. (2004) Biología de la conservación del águila-azor perdicera Hieraaetus fasciatus en España: investigación científica y gestión. Ardeola 51: 459–468.Google Scholar
Palomares, F. (2001) Comparison of 3 methods to estimate rabbit abundance in a Mediterranean environment. Wildl. Soc. Bull. 29: 578–585.Google Scholar
Palomares, F., Delibes, M., Revilla, E., Calzada, J. and Fedriani, J. M. (2001) Spatial ecology of Iberian lynx and abundance of European rabbits in southwestern Spain. Wildl. Monogr. 148: 1–36.Google Scholar
Parellada, X. (1984) Variació del plomatge i identicació de l′aliga cuabarrada (Hieraaetus fasciatus fasciatus). Rapinyaires Mediterranis 2: 70–79.Google Scholar
Parellada, X., De Juan, A. and Alamany, O. (1984) Ecologia de l′aliga cuabarrada (Hieraaetus fasciatus): factors limitants, adaptacions morfológiques i ecológiques i relacions interespecífiques amb l′aliga daurada (Aquila chrysaetos). Rapinyaires Mediterranis 2: 121–141.Google Scholar
Penteriani, V., Balbontin, J. and Ferrer, M. (2003) Simultaneous effects of age and territory quality on fecundity in Bonelli’s Eagle Hieraaetus fasciatus. Ibis 145: 77–82.CrossRefGoogle Scholar
Penteriani, V., Otalora, F. and Ferrer, M. (2008) Floater mortality can explain the Allee effect in animal populations. Ecol. Model. 213: 98–104.CrossRefGoogle Scholar
Penteriani, V., Otalora, F., Sergio, F. and Ferrer, M. (2005) Environmental stochasticity in dispersal areas can explain the ‘mysterious’ disappearance of breeding populations. P. Roy. Soc. Lond. B 272: 1265–1269.Google ScholarPubMed
Quinn, G. P. and Keough, M. J. (2003) Experimental design and data analysis for biologists. Cambridge, UK: Cambridge University Press.Google Scholar
Real, J. (2004) Águila-Azor Perdicera, Hieraaetus fasciatus. Pp. 154–157 in Madroño, A., González, C. and Atienza, J. C., eds. Libro Rojo de las aves de España. Madrid, Spain: Dirección General para la Biodiversidad-Seo/BirdLife.Google Scholar
Real, J., Grande, J. M., Mañosa, S. and Sánchez-Zapata, J. A. (2001) Causes of death in different areas for Bonelli’s Eagle Hieraaetus fasciatus in Spain. Bird Study 48: 221–228.CrossRefGoogle Scholar
Rogers, J. M., Arthur, C. P. and Soriguer, R. C. (1994) The rabbit in continental Europe. Pp. 22–63 in Thomson, H. V. and King, C. M., eds. The European rabbit: the history and biology of a successful colonizer. Oxford, UK: Oxford University Press.CrossRefGoogle Scholar
Rollan, A., Real, J., Bosch, R., Tintó, A. and Hernández-Matías, A. (in press). Modelling the risk of collision with power lines in Bonelli’s Eagles Hieraaetus fasciatus and its implications for conservation. Bird Conservation International. doi:10.1017/S0959270910000250Google Scholar
Sánchez-Zapata, J. A. and Calvo, J. F. (1999) Raptor distribution in relation to landscape composition in semi-arid Mediterranean habitats. J. Appl. Ecol. 36: 254–262.CrossRefGoogle Scholar
Sergio, F., Marchesi, L. and Pedrini, P. (2004) Integrating individual habitat choices and regional distribution of a biodiversity indicator and top predator. J. Biogeogr. 31: 619–628.Google Scholar
Serrano, D. (1998) Diferencias interhábitat en la alimentación del Búho Real (Bubo bubo) en el valle medio del Ebro (NE de España): efecto de la disponibilidad de conejo Oryctolagus cuniculus. Ardeola 45: 35–46.Google Scholar
Siegel, S. and Castellan, N. J. Jr. (1988) Non-parametric statistics for the behavioral sciences. 2nd edition. Singapore: McGraw-Hill.Google Scholar
Sokal, R. R. and Rohlf, F. J. (1995) Biometry. 3rd edition. New York, USA: Freeman.Google Scholar
Soriguer, R. C. (1981) Estructura de sexos y edades en una población de conejos (Oryctolagus cuniculus L.) en Andalucía occidental. Doñana, Acta Vertebrata 8: 225–236.Google Scholar
Soriguer, R. C. and Rogers, P. M. (1981) The European wild rabbit Oryctolagus cuniculus L. in Mediterranean Spain. Pp. 600–613 in K. Myers and C. D. MacInnes, eds. Proc. of the first World Lagomorph Conference, Ontario, Canada: Univ. Guelph.Google Scholar
Soriguer, R. C., Pérez, J. M. and Fandos, P. (1997) Teoría de censos: aplicación al caso de los mamíferos. Galemys 9: 15–37.Google Scholar
Soulé, M. E. and Wilcox, B. (1980) Conservation biology: an evolutionary-ecological perspective. Sunderland, Mass: Sinauer Associates.Google Scholar
Soutullo, A., Urios, V., Ferrer, M. and Peñarrubia, S. G. (2006) Postfledging behaviour in Golden Eagles: onset of the juvenile dispersal and progressive distancing from the nest. Ibis 148: 307–312.CrossRefGoogle Scholar
Soutullo, A., López-López, P. and Urios, V. (2008a) Incorporating spatial structure and stochasticity in endangered Bonelli’s eagle’s population models: Implications for conservation and management. Biol. Conserv. 141: 1013–1020.Google Scholar
Soutullo, A., Urios, V., Ferrer, M. and López-López, P. (2008b) Habitat use by juvenile Golden Eagles Aquila chrysaetos in Spain. Bird Study 55: 236–240.CrossRefGoogle Scholar
Valkama, J., Korpimäki, E., Arroyo, B., Beja, P., Bretagnolle, V., Bro, E., Kenward, R., Mañosa, S., Redpath, S. M., Thirgood, S. and Viñuela, J. (2005) Birds of prey as limiting factors of gamebird populations in Europe: A review. Biol. Rev. 80: 171–203.Google Scholar
Vargas, J. M., Guerrero, J. C., Farfán, M. A., Barbosa, A. M. and Real, R. (2006) Land use and environmental factors affecting Red-legged Partridge (Alectoris rufa) hunting yields in southern Spain. Eur. J. Wildlife. Res. 52: 188–195.CrossRefGoogle Scholar
Villafuerte, R., Viñuela, J. and Blanco, J. C. (1998) Extensive predator persecution caused by population crash in a game species: the case of Red Kites and rabbits in Spain. Biol. Conserv. 84: 181–188.Google Scholar
Watson, J. (1997) The Golden Eagle. London, UK: T. and A. D. Poyser.Google Scholar
Willians, B. K. and Titus, K. (1988) Assessment of sampling stability in ecological applications of discriminant analysis. Ecology 69: 1275–1285.Google Scholar
Figure 0

Figure 1. Study area showing settlement (solid circles) and non-settlement (empty circles) areas for Bonelli’s and Golden Eagles in Southern Spain. Numbers refer to the number of 9-km2 squares sampled in each area. For details, see the Methods section.

Figure 1

Table 1. Variables used (except geographical ones), their values, and comparison (Student’s t- test) between settlement and non-settlement areas of large diurnal raptors (Bonelli’s and Golden Eagles) in southern Spain. Sampling unit was 3 × 3 km square (UTM grid system). More information in the Methods section. Asterisks indicate significance after Bonferroni sequential correction.

Figure 2

Table 2. Mean, standard deviation (SD), and comparison (Student’s t-test) for variables in settlement areas with presence of Bonelli’s and Golden Eagles in southern Spain.