Introduction
Climate change is recognised as one of the most important drivers of the current loss of biological diversity (IPCC Reference Pachauri and Meyer2014). To date, most studies on climate change have predominantly focused on the direct effects of rising temperatures (Thuiller Reference Thuiller2007), increasing carbon dioxide levels (Meehl and Washington Reference Meehl and Washington1996), or sea-level rise (Runting et al. Reference Runting, Wilson and Rhodes2013). However, the indirect impacts of climate change on ecosystems, such as changes in hydrological cycles and increasing magnitude and frequency of extreme weather events (i.e. floods, droughts, and cyclones) have been less often analysed (Rahmstorf and Coumou Reference Rahmstorf and Coumou2011, Ummenhofer and Meehl Reference Ummenhofer and Meehl2017; reviewed by Maxwell et al. Reference Maxwell, Butt, Maron, McAlpine, Chapman, Ullmann and Watson2019). Climate influences all living organisms since individuals are adapted to occupy their niche according to their biological requirements (Soberon and Peterson Reference Soberón and Peterson2005). Therefore, abnormal variations on climate will likely impact the survival, breeding success, and phenology of species (Crick Reference Crick2004, Carey et al. Reference Carey2009, Reichert et al. Reference Reichert, Cattau, Fletcher, Kendall and Kitchens2012, Maxwell et al. Reference Maxwell, Butt, Maron, McAlpine, Chapman, Ullmann and Watson2019). The frequency and intensity of extreme weather events are predicted to increase in many regions of the world due to climate change, creating a new threat for many species (Easterling and Karl Reference Easterling and Karl2001, Meehl and Tebaldi Reference Meehl and Tebaldi2004, IPCC Reference Pachauri and Meyer2014, Maxwell et al. Reference Maxwell, Butt, Maron, McAlpine, Chapman, Ullmann and Watson2019). Indeed, understanding the impacts of extreme climatic events on populations and ecosystems is considered one of the factors of greatest importance to protect biological diversity (Sutherland et al. Reference Sutherland, Adams, Aronson, Aveling, Blackburn, Broad and Watkinson2009).
Among the extreme climate events there are those associated with cold events, such as storms, snowfalls, and cold waves (extreme cold events hereinafter). Extreme cold events may pose a great risk for bird survival (Formenti et al. Reference Formenti, Viganó, Bionda, Ferrari, Trogu, Lanfranchi and Palme2015, Krause et al. Reference Krause, Pérez, Chmura, Sweet, Meddle, Hunt and Wingfield2016), even when they are time restricted. For example, Sanders et al. (Reference Sanders, Mawson and Dawson2011) estimated that around 12% of a population of the threatened Carnaby’s Black Cockatoos Calyptorhynchus latirostris were found dead after a two-hour storm. Nonetheless, the real impact was likely much greater since several individuals would have died but remained undetected (Sanders et al. Reference Sanders, Mawson and Dawson2011). Beyond the direct impact of extreme cold events on bird survival, previous studies have also found that cold events may directly limit food intake, cause thermal challenges to energy balance (Ramakrishnan et al. Reference Ramakrishnan, Sivasubramanian, Ramkumar and Ramasubramanian2013), affect population dynamics via carry-over effects on breeding success in the subsequent breeding season (Järvistö et al. Reference Järvistö, Calhim, Schuett, Sirkiä, Velmala and Laaksonen2016), or create prolonged stress on birds (Rogers et al. Reference Rogers, Ramenofsky, Ketterson, Nolan and Wingfield1993, Liu et al. Reference Liu, Hu, Kessler, Gong, Wang, Li and Li2018), which may suppress the immune function and health of the individuals.
The negative impact of extreme cold events on bird species may be enhanced on 1) those living at higher elevations, such as uplands, where the frequency and the intensity of extreme cold events are more pronounced (reviewed by Scridel et al. Reference Scridel, Brambilla, Martin, Lehikoinen, Iemma, Matteo and Chamberlain2018), and on 2) smaller body passerines adapted to warmer conditions (Cohen et al. Reference Cohen, Fink and Zuckerberg2021). Similarly, species with a high degree of habitat specialisation might be more prone to being affected by extreme cold events, since generalist species usually occupy a wide range of habitats and feed on different kinds of food. Populations of specialists and threatened species are usually spatially isolated, which increases their vulnerability to stochastic and extreme weather events and reduces their dispersal ability among habitat patches (Bech et al. Reference Bech, Boissier, Drovetski and Novoa2009, Fjeldså et al. Reference Fjeldså, Bowie and Rahbek2012). Finally, the negative impacts of extreme cold events might be even worse for insectivorous birds, especially residents that are present year around, because these species might be unable to find food resources for a long period of time following a snowfall event, and consequently may be displaced (Rajchard et al. Reference Rajchard, Procházka and Kindlmann2006, Scridel et al. Reference Scridel, Brambilla, Martin, Lehikoinen, Iemma, Matteo and Chamberlain2018). However, our current knowledge on the impact of extreme cold events on population dynamics of resident insectivorous bird species is limited, since these events are stochastic and threatened species are intrinsically difficult to monitor.
In January 2021 Storm Filomena, one of the largest snowstorms in the last 50 years in Spain, hit a large part of continental Spain (Figure 1). The storm lasted from 7 January to 10 January 2021 and was followed by a cold wave the following week, from 11 January to 17 January 2021 (Smart Reference Smart2021). Both phenomena, the snowstorm and the cold wave, were officially catalogued as historic meteorological events by the Spanish Meteorological Agency (AEMET 2021). The snowstorm covered the interior of the Iberian Peninsula with historically deep accumulations of snow. For example, the snow fell continuously over 30 hours in the city of Madrid (central Spain), leaving more than 50 cm of accumulated snow (Tapiador et al. Reference Tapiador, Villalba-Pradas, Navarro, Martín, Merino, García-Ortega and Sánchez2021), which exceeded all historical events of the last century (Smart Reference Smart2021). Indeed, the whole region of Madrid and the region of Castilla-La Mancha were also declared “catastrophe areas” by the national government, and several other regions in south, central, and eastern Spain were also highly affected by the snowstorm (Figure 1). There were snowfall accumulations of 50 cm in several areas of central Spain and about 25 cm in eastern Spain, such as in Zaragoza and the Ebro Valley (Rodríguez-Sánchez et al. Reference Rodríguez-Sánchez, Granda-Maestre, Calvo-Sancho and Oliver-García2021). The cold wave in the week following the snowfall was marked by minimum air temperatures between -5ºC and -15ºC in the most affected areas. The cold wave broke historical records of minimum air temperatures in several regions of Spain, with recorded official temperatures of up to -26.5ºC in Torremocha de Jiloca (Teruel province), but even lower temperatures (e.g. -33.6ºC in Checa-Vasequilla, Guadalajara province) at unofficial sites (AEMET 2021). Owing to the heavy snowfall and low temperatures during the preceding week, the snow lasted several days (up to two weeks in some areas) and caused major disruptions to daily life in Spain at the height of the COVID-19 pandemic (Smart Reference Smart2021).
Figure 1. Evolution of the snow cover and land surface temperature in the Iberian Peninsula during Storm Filomena. The snow cover was extracted from the modis product MOD10A1 that provides a daily composite of snow cover at a 500-m spatial resolution. Land surface temperature was estimated from Modis 8-days product MOD11A2 that provides an average 8-day per-pixel land surface temperature and Emissivity (LST&E) with a 1-km spatial resolution. Temperatures below zero are represented by blue colours and temperatures above zero up to 25°C are represented by green to yellow, orange, and red, respectively.
Currently, there is a need to assess the adaptive potential of birds and other organisms to unpredictable, extreme weather events as a result of climate change (Van der Pol et al. Reference Van der Pol, Ens, Heg, Brouwer, Krol, Maier and Koffijberg2010). In this paper, we aim to document the short-term impact of extreme cold events, using Storm Filomena as a case study, on the abundance of an insectivorous, specialist, and threatened bird species in the breeding season following the storm. Given the increasing frequency and severity of extreme weather events over the world due to climate change, we hope our findings might be useful to better understand how extreme cold events may impact the population dynamics of birds.
Methods
Study species
We selected Dupont’s Lark Chersophilus duponti as target species to assess the impact of extreme cold events on the distribution of birds. We chose that species because it is classified as a Vulnerable globally threatened insectivorous bird (Goméz-Catasús et al. 2018, García-Antón and Traba Reference García-Antón and Traba2021, BirdLife International 2020) with limited dispersal movements and patchy distribution (Laiolo et al. 2017, Pérez-Granados et al. Reference Pérez-Granados, Sáez-Gómez and López-Iborra2022). The European population of Dupont’s Lark, which is restricted to Spain, has declined over 40% during the period 2004–2015 (Gómez-Catasús et al. Reference Gómez-Catasús, Pérez-Granados, Barrero, Bota, Giralt, López-Iborra and Traba2018), and has been predicted to be extinct in two to three decades (García-Antón and Traba Reference García-Antón and Traba2021). The current distribution of the species is extremely fragmented (García-Antón et al. 2020) and ranges from sea level up to 1,400 m a.s.l., although its main populations, such as those in the Iberian System and the Ebro Valley, are located above 1,000 m a.s.l. The fragmented distribution of the species is due to its strong dependence on flat, low shrub natural steppes (Garza et al. Reference Garza, Suárez, Herranz, Traba, García De La Morena, Morales and Castañeda2005, Pérez-Granados et al. Reference Pérez-Granados, Lopez-Iborra and Seoane2017, Gómez-Catasús et al. Reference Gómez-Catasús, Garza, Morales and Traba2019), a habitat type in decline in Iberia due to long-term habitat transformation. The species has been catalogued as resident (Suárez et al. Reference Suárez, Garcia, Sampietro and Garza2006), overwintering above 1,000 m a.s.l., and defined as a poor disperser, with mean breeding dispersal movements around 100–150 m (Laiolo et al. Reference Laiolo, Vögeli, Serrano and Tella2007, Pérez-Granados et al. Reference Pérez-Granados, Sáez-Gómez and López-Iborra2022). However, there are a few documented cases of individuals wintering outside their breeding areas and performing dispersive movements over 30 km (Suárez et al. Reference Suárez, Garcia, Sampietro and Garza2006, García-Antón et al. Reference García-Antón, Garza and Traba2015), which together with recent studies about metapopulations’ connectivity (García-Antón et al. Reference García-Antón, Garza and Traba2021), suggest that the species might be able to perform longer dispersals than previously thought. Indeed, Suárez et al. (Reference Suárez, Garcia, Sampietro and Garza2006) proposed that the whole population in a given area may perform temporal movements in response to exceptional weather conditions, such as heavy snowfalls. Due to its threat status, the extreme fragmentation of its optimal habitat, its small body size and aspects of its ecology (i.e. insectivory, ground-foraging behaviour, and poor ability to disperse), we considered Dupont’s Lark to be an interesting model for the analysis of the impact of extreme cold events on a species at risk.
Bird monitoring
We collected data either annually or every two years for 14 Dupont’s Lark subpopulations during the 2017–2021 period. We defined a subpopulation as all habitat patches separated by 5 km or less (following García-Antón et al. Reference García-Antón, Garza and Traba2021). To facilitate reading we use the term population hereinafter. Surveyed populations covered most of the entire Iberian distribution of the species and hosted around 380 males in 2017 (c.10% of the European population) (Traba et al. Reference Traba, Garza, García-Antón, Gómez-Catasús, Zurdo, Pérez-Granados and M. B. Morales2019).
Dupont’s Lark censuses were carried out during the breeding season (mid-March–mid-June). Birds were counted during the hour before sunrise by linear transect (500 m inner belt width) or territory mapping (three to four visits), during which vocalising males were annotated with the help of a GPS. Both counting methods produced very similar estimates (see Pérez-Granados and López-Iborra Reference Pérez-Granados and López-Iborra2017). Estimated population size refers to the minimum number of males detected (line transect method) or territories defined (mapping method). Censuses were always performed under adequate weather conditions (e.g. no rain, low wind) and at constant speed. Each population was always surveyed by the same researcher team using the same counting method and repeating the same line transects throughout the study period, which allows inter-annual comparisons within the same population.
Statistical analyses
We estimated the population change of the monitored populations from the formula:
$$ \mathrm{Population}\ \mathrm{change}\hskip0.35em =\hskip0.35em \left(\left({N}_{\mathrm{p}}/{N}_i\right)\hat{\mkern6mu} (1/\mathrm{years}\right)-1 $$
where Np is the estimated population for one area for a specific year, N i is the estimated population in the same area in the previous census, and years is the number of years between the estimates. These values were then multiplied by 100 to yield growth rates in percentages.
To assess the impact of Storm Filomena on the population dynamics of Dupont’s Lark we estimated the mean population variation of the monitored populations for the following three periods: 1) control period (13 populations monitored between 2017 and 2020); 2) impact period (seven populations monitored the year before and the year after the storm, 2020 and 2021); 3) extended impact period (14 populations monitored two years before the storm and the year after, 2019 and 2021). We included the “extended impact period” to have an estimate of the impact of the storm on a larger number of populations. Whenever possible we used the largest elapsed time between censuses for the control period. For example, for those populations monitored annually, the annual variation for the control period was considered as the one that occurred between 2017 and 2020, while for the other five populations monitored during the control period the largest elapsed time was from 2017 to 2019 (see Table 1). To evaluate whether the population decline of Dupont’s Lark was higher following Storm Filomena than during the control period, we fitted two one-sided Wilcoxon signed-rank tests (paired samples). We opted for a one-sided test since we hypothesised that the population decline would be higher owing to the storm impact. The first Wilcoxon test was run on the 13 populations for which there were data available to compare the population change during the control period with that obtained during the extended impact period, while the second test was fitted for only the seven populations with data available to compare the magnitude of change that occurred between the control and the impact period. The results are expressed as mean ± SE. The Wilcoxon signed-rank tests were conducted in R 3.6.2 (R Development Core Team 2019) using the wilcox.test function. The level of significance was P <0.05.
Table 1. The number of Dupont’s Lark males detected per year for each monitored population, as well as the population growth rate (in %) for the control period (2017–2020) and following Storm Filomena. For the rest of the monitored populations, the annual variation due to the impact of Storm Filomena was estimated with data collected two years before the storm (2019) and one year after (2021). The total number of males detected for the three years (2017, 2019, and 2021) when all populations were monitored is also given.
* One population was not monitored.
Results
The overall monitored Dupont’s Lark population size decreased from 381 males in 2017 (one population first counted in 2019) to 146 males in 2021 (Table 1), with the local extinction of five populations following Storm Filomena, which represents 26.3% of the set of study populations (Table 1). The monitored populations suffered an average 19.4% decline during the control period (±5.0, SE, n = 13 populations), while the overall decline after Storm Filomena was 67.6% (±9.4, n = 14 populations monitored between 2019 and 2021). When considering only the seven populations monitored the year before and after Storm Filomena, the impact of the extreme weather event was even greater, with an overall decline of 66.5% (±15.9) (Figure 2). There was a significantly higher population decline following Storm Filomena than during the control period, both when considering the extended impact period (Wilcoxon signed-rank test: n = 13, Z = -3.33, V = 87, P <0.001) and the impact period (Wilcoxon signed-rank test: n = 7, Z = -2.27, V = 26, P = 0.023).
Figure 2. Estimated population sizes, in number of males, for seven populations of Dupont’s Lark monitored annually during the 2017–2021 period. The vertical dashed line shows when Storm Filomena occurred, while the coloured numbers represent the population variation between 2020 and 2021. Letters identify populations as named in Table 1.
Discussion
In this study we found evidence of a drastic population change for the threatened Dupont’s Lark following Storm Filomena, an extreme cold event. The year after the storm the monitored populations suffered a mean reduction of over 65%, which was more than three times higher than the mean decline observed during the control period and much higher than the average annual decrease estimated for a set of 92 Iberian populations during the period 2004–2015 (-3.9%) (Gómez-Catasús et al. Reference Gómez-Catasús, Pérez-Granados, Barrero, Bota, Giralt, López-Iborra and Traba2018). The differences found in population annual variation between the control and the storm period were significant, and the extreme cold event also resulted in the local extinction of up to five small populations of Dupont’s Lark. Although our dataset was limited, it comprised around 10% of the estimated European Dupont’s Lark population. Therefore, we believe that our results, although not conclusive, may be representative of the impact of Storm Filomena on Dupont’s Lark, whose entire population may have been heavily impacted. Our results are in agreement with previous studies which also found that extreme weather events may strongly impact bird populations in the short term (Sanders et al. Reference Sanders, Mawson and Dawson2011, Formenti et al. Reference Formenti, Viganó, Bionda, Ferrari, Trogu, Lanfranchi and Palme2015, Krause et al. Reference Krause, Pérez, Chmura, Sweet, Meddle, Hunt and Wingfield2016).
Storm Filomena temporarily reduced habitat availability and the quality of several habitat patches occupied by the species, especially in high altitude areas, as habitat patches at higher altitudes were fully covered with snow for several days (Deshpande et al. Reference Deshpande, Lehikoinen, Thorogood and Lehikoinen2022). According to official data provided by AEMET, there was snow cover for a mean of 11.1 days across the localities of the 14 populations included in the 2019–2021 dataset (mean of 10.8 days for the seven populations monitored in 2020 and 2021). The presence of snow cover for such an extended period likely caused a challenge for Dupont’s Lark to find food resources due to the insectivorous habits of the species (Rajchard et al. Reference Rajchard, Procházka and Kindlmann2006, Scridel et al. Reference Scridel, Brambilla, Martin, Lehikoinen, Iemma, Matteo and Chamberlain2018). Indeed, the bulk of the diet is composed of terrestrial and hypogeal arthropods, such as spiders and beetles (Herranz et al. Reference Herranz, Yanes and Suárez1993, Talabante et al. Reference Talabante, Aparicio, Aguirre and Peinado2015), which were covered by the snow during this period. Such limitations may have compromised the survival probability of the species and/or may have forced individuals to perform long spatial displacements looking for optimal habitats (i.e. lower altitude not covered by snow). In fact, there is some historical and recent data that reinforce this idea. In the winter of 1963, after heavy snowfalls at the inland Iberian Peninsula, several individuals of Dupont’s Lark were observed in February at the Mediterranean coast far from any breeding population (Torredembarra, Tarragona province, north-eastern Spain), where they remained for several weeks (Mestre Reference Mestre1967). During Storm Filomena, on 13 January 2021, one Dupont’s Lark was sighted at the Mediterranean coast (Marjal del Moro, Valencia province, eastern Spain) (Arribas Reference Arribas2021), where there are no known populations or previous records of the species within a radius of 100 km (Pérez-Granados and López-Iborra Reference Pérez-Granados and López-Iborra2013). The bird remained in the area for around two weeks and afterwards it was not seen again. Another interesting record occurred in the urban area of the small village of Tornos (Teruel province, central Spain, 201 inhabitants in 2021), where a ringed Dupont’s Lark was found dead; this is a habitat typically avoided by this specialist species. This bird had been ringed in the preceding breeding season at Embid (Guadalajara province, central Spain), 24 km away. It has been suggested that the bird moved to feed in this urban area which had been cleared of snow (Fuertes Reference Fuertes2021). These anecdotal records suggest that the species was forced to leave the breeding areas, at least temporarily, to non-optimal habitats, which may have compromised its survival.
Alarmingly the species suffered a mean annual decline of 19% during the control period, although it is in agreement with previous studies that also described the current decline of Dupont’s Lark (e.g. Tella et al. Reference Tella, Vögeli, Serrano and Carrete2005, Pérez-Granados and López-Iborra Reference Pérez-Granados and López Iborra2014, Gómez-Catasús et al. Reference Gómez-Catasús, Pérez-Granados, Barrero, Bota, Giralt, López-Iborra and Traba2018). This declining trend threatens the persistence of the species by increasing the isolation and fragmentation of the remaining habitat patches. In 2018 the European Dupont’s Lark population was estimated to be around 1,400–1,800 breeding pairs (Traba et al. 2019). These estimates could be corrected by applying a correction factor of 0.32 according to the mean decline of 68% owing to Storm Filomena. Therefore, the European Dupont’s Lark population would be estimated currently to be around 448–576 breeding pairs. However, this estimate may have some uncertainties (e.g. due to the reduced number of regions and sampled sites for monitoring the impact of the storm), and further monitoring programmes are needed for estimating the European population size with increased accuracy.
Our results agree with Hendricks and Norment (Reference Hendricks and Norment1992) who found that a severe snowstorm had an important role in the population dynamics of the American Pipit Anthus rubescens, and the storm’s impact was greater in small and peripheral habitat patches. We found that five small populations of Dupont’s Lark (mean size 3.6 males, range 1–12) were extirpated after Storm Filomena. It is possible that the individuals comprising these small populations may have died due to the extreme cold event (e.g. thermal challenges to energy balance or reduced immune function), or that the individuals may have occupied a different habitat patch once they returned. For example, returning individuals may have selected to settle in occupied patches since the presence of co-specifics seems to guide migrating Dupont’s Lark by advertising habitat quality (Laiolo and Obeso Reference Laiolo and Obeso2012). The recurrent impact of extreme weather events may negatively affect the metapopulation dynamics of Dupont’s Lark, given the small size of populations, and therefore proactive actions that aid the species in adapting to climate change (i.e. increasing habitat connectivity and intra-species genetic variation), which have been shown to benefit species threatened by extreme events, may be needed (Maxwell et al. Reference Maxwell, Butt, Maron, McAlpine, Chapman, Ullmann and Watson2019). Dupont’s Lark populations may also benefit from more active actions, such as the translocation of individuals following successive extreme weather events (see a similar approach for flood events in Sousa et al. Reference Sousa, Varandas, Cortes, Teixeira, Lopes-Lima, Machado and Guilhermino2012). Indeed, the habitat of the only monitored population whose abundance increased after Storm Filomena, despite snow cover for the same amount of days (Barahona-Rello, Soria province, 73 males in 2020 and 86 in 2021) (Figure 2A), was actively managed during the spring of 2018 by the LIFE Ricotí programme. In that area the number of trees was reduced and extensive grazing was promoted to increase habitat availability and improve habitat quality for Dupont’s Lark by increasing food availability associated with sheep dung (see Gómez-Catasús et al. Reference Gómez-Catasús, Traba, Reverter, Zurdo, Barrero, Bustillo-de la Rosa and Santamaría2021, Reverter et al. Reference Reverter, Gómez-Catasús, Barrero and Traba2021). This preliminary finding suggests that active management of habitat patches focused on increasing habitat quality and availability might be a feasible solution to increase the viability of Dupont’s Lark populations.
Besides the strong short-term negative impact of Storm Filomena on population dynamics, such extreme weather events could also have some positive impacts in the context of long-term population dynamics. Previous research suggests that extreme cold events may force Dupont’s Larks to perform much longer movements than expected under normal conditions (Mestre Reference Mestre1967, Arribas Reference Arribas2021, Fuertes Reference Fuertes2021), which might be particularly true for our target species, which have been defined as having low breeding dispersal ability (Laiolo et al. Reference Laiolo, Vögeli, Serrano and Tella2007, Pérez-Granados et al. Reference Pérez-Granados, Sáez-Gómez and López-Iborra2022). It has also been shown in other bird species that extreme weather events, like strong winds, can result in colonisation of areas where they had not previously occurred (Cortés-Avizanda and Tavecchia, Reference Cortés-Avizanda and Tavecchia2021). Future research should try to elucidate the role that extreme weather events may play in maintaining gene flow among Dupont’s Lark populations (Méndez et al. Reference Méndez, Tella and Godoy2011), or in local extinction and recolonisation processes in isolated populations such as the case observed in Catalonia, where Dupont’s Lark was seen a decade after becoming locally extinct (Gómez-Catasús et al. Reference Gómez-Catasús, Pérez-Granados, Barrero, Bota, Giralt, López-Iborra and Traba2018). These events may play a role in the long-term population dynamics of threatened and patchily distributed species, such as Dupont’s Lark (Frederiksen et al. Reference Frederiksen, Daunt, Harris and Wanless2008).
In this study we have described the drastic population decline of Dupont’s Lark after an extreme cold event. Due to the low number of studies assessing how extreme climatic events can impact bird populations and the expected increase in frequency and severity of extreme weather events over the following decades due to climate change, our findings are useful to improve understanding of the impacts of extreme cold events on the population dynamics of birds. Our results may also be useful for future studies with the species (or similar ones) aimed at understanding the impact of stochastic events on population dynamics (e.g. population viability analyses, climate change projections). Further studies may assess the impact of extreme weather events on both adult and juvenile survival and on subsequent reproductive success (Järvistö et al. Reference Järvistö, Calhim, Schuett, Sirkiä, Velmala and Laaksonen2016), to gain a more comprehensive view of the role that catastrophic events can have on long-term population dynamics.
Acknowledgements
This study was partially funded by the LIFE Ricoti programme (LIFE15-NAT-ES-000802), supported by the European Commission, Levantina y Asociado de Minerales, S.A., with the project “Estudios de investigación aplicado a la conservación de las poblaciones de alondra ricotí (Chersophilus duponti) en el entorno del municipio de Vallanca”, and by the Dirección General de Política Forestal y Espacios Naturales de la Junta de Comunidades de Castilla La Mancha with the project “SSCC/046/2017 Censo de Alondra ricotí en la provincia de Guadalajara. Año 2017”, Censuses in Catalonia were carried out with the support of the Generalitat of Catalonia. CPG acknowledges the support from the Ministerio de Educación y Formación Profesional through the Beatriz Galindo Fellowship (Beatriz Galindo – Convocatoria 2020).
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