Coordination across administrative units can be an imperative for the management and, especially, the monitoring, of shared wildlife populations. In many cases such coordination does not occur and jurisdictional differences in management practices affect adjacent or shared populations. For example, national parks, where hunting is usually forbidden, are typically surrounded by hunting areas where the harvest can be significant. In contrast, when populations of threatened large carnivores or raptors overlap jurisdictions, coordinated management is relatively common (Proctor et al., Reference Proctor, Servheen, Miller, Kasworm and Wakkinen2004; Antor et al., Reference Antor, Margalida, Frey, Heredia, Lorente and Sesé2007).

Ungulates have life histories that are conducive to sustainable harvests (Caughley & Sinclair, Reference Caughley and Sinclair1994) and, for a variety of reasons (population control, meat production, and recreational and trophy hunting), are intensively exploited. In addition, threatened populations have recovered (e.g. Arabian oryx Oryx leucoryx, IUCN SSC Antelope Specialist Group, 2008) and conservation efforts can have a positive effect (e.g. bison Bison bonasus, Pucek, Reference Pucek2004; Apennine chamois Rupicapra pyrenaica ornata, Dupré et al., Reference Dupré, Monaco and Pedrotti2001) although, in some cases, conservation efforts have been initiated too late (e.g. Pyrenean wild goat Capra pyrenaica; García-González & Herrero, Reference García-González and Herrero1999). In some instances ungulate species have spread in response to socio-economic changes (Gortázar et al., Reference Gortázar, Herrero, Villafuerte and Marco2000) or unintentional escapes (Goulding et al., Reference Goulding, Roper, Smith and Baker2003). In the case of mountain ungulates populations have been created ex novo (e.g. Apennine chamois and Alpine ibex Capra ibex; Mari & Lovari, Reference Mari and Lovari2006; Aulagnier et al., Reference Aulagnier, Kranz, Lovari, Jdeidi, Masseti and Nader2009), and the size and distributions of populations have increased through reintroductions or re-enforcements (Berducou, Reference Berducou1990; Moço et al., Reference Moço, Guerreiro, Ferreira, Rebelo, Loureiro, Petrucci-Fonseca and Pérez2006). Legislation has ensured that appropriate hunting quotas are set and that thereby the standards for the sustainable use of the species are met.

The Pyrenean chamois Rupicapra pyrenaica pyrenaica is a small, slightly dimorphic mountain-dwelling ungulate endemic to the Pyrenees. It is subject to intense hunting pressure, although hunting is banned in several national parks and nature reserves. In 2004 the population was at least 55,000 animals (Herrero et al., Reference Herrero, Escudero, Fernández de Luco and García-González2004). In the three Pyrenean countries (Andorra, France and Spain) the Pyrenean chamois is a game species and is an important economic and social resource in rural communities in Spain and a significant non-profit recreational activity in France.

At the western limit of its current distribution the chamois occupies an area that is managed independently by the autonomous governments of Navarre and Aragon, Spain, whose management goals differ significantly. The subspecies is categorized as Vulnerable on the Red List for Navarre but not threatened, and huntable, in neighbouring Aragon. Most of the area inhabited by chamois in this area lies within a nature reserve in Navarre and a game reserve in Aragon.

If coordinated management decisions can help achieve the objectives set for wildlife populations that encompass multiple jurisdictions and if the benefits of cooperation can be greatest for populations near their distributional limit, chamois at the western limit of their range in the Pyrenees provide a suitable evaluation of the efficacy of this approach. Here, we assess whether the recovery of the Pyrenean chamois population (the management goal) was correlated with management decisions: the temporary ban on hunting in Aragon and an increase in coercive force (the number of rangers) in Navarre.

The study area includes three mountain massifs above 1,600 m (Ezkaurre, 745 ha; Larra–Lapaquiza, 10,588 ha; Lakartxela, 666 ha; Fig. 1), with mixed forests of beech Fagus sylvatica, fir Abies alba and Scots pine Pinus sylvestris, and mountain pine Pinus uncinata woodlands and cliffs and meadows. The maximum elevation is 2,500 m. In Navarre the study area includes Larra–Belagoa Nature Reserve, and in Aragon the entire study area is contained within Los Valles Game Reserve. In these areas chamois coexist with domestic livestock (cattle, horses and sheep) and other wild ungulates (wild boar Sus scrofa, and roe Capreolus capreolus and red deer Cervus elaphus).

Fig. 1

The study area, showing the three massifs of Lakartxela, Larra–Lapaquiza and Ezkaurre inhabited by the Pyrenean chamois Rupicapra pyrenaica pyrenaica in the westernmost part of its distribution.

The first estimate of the chamois population in this area was in 1992 (Garin & Herrero, Reference Garin and Herrero1997). This indicated the small size of the population and led to a ban on hunting in western Los Valles Game Reserve in 1993. In Navarre, after the number of rangers increased from one to six, coordinated long-term monitoring of the chamois population began, in 1996. New rangers attended a course on chamois biology and survey methods. In Aragon the number of experienced rangers was not a limiting factor and monitoring began in 1995. Rangers from Navarre and Aragon, technicians, volunteers and ourselves participated in surveys, which were conducted from dawn until midday in June and November, to 2007, under a common, coordinated plan based on an agreement between the two jurisdictions. Monitoring involved simultaneous annual counts of individuals in both Navarre and Aragon by observation along 10 itineraries. In addition, we surveyed one itinerary in the Lakartxela massif, also in June and November, an area where chamois had existed historically (Fig 1). Since 2002, when chamois appeared there for the first time, two new itineraries were added to this area. Pairs of observers equipped with binoculars, spotting scopes, local maps and radio receivers walked each itinerary. The location of each group of chamois was plotted on a map and the sex and age (adult males, adult females, yearlings and kids) of individuals noted. A group was any animal aggregation that occupied the same parcel of land, had sensorial contact and was more or less coordinated in its movements (Schaller, Reference Schaller1977). The number of individuals recorded was an estimate of the minimum population size but provided a basis for an analysis of any population trend. Population density was based on the amount of area above 1,600 m. To identify population trends we used a Poisson regression to fit the data to an exponential growth model and calculated the annual growth rate.

In 1995 the Ezkaurre massif had at least 33 chamois and in 2007 at least 136 (5.1 chamois km^-2; Fig. 2). In the 13 years of surveys the number of chamois observed in the two census periods of any given year sometimes differed significantly and therefore the estimated rate of exponential growth was based on the higher of the numbers observed in June and November. The exponential growth rate was 0.1386 ± SE 0.01 (likelihood test P < 0.0001), i.e. an average annual increase of 15% (seven chamois year^-1). In 1996 the Larra–Lapaquiza massif had at least 144 chamois and in 2007 at least 455 (12.2 chamois km^-2; Fig. 2). In the 12 years of surveys the exponential growth rate was 0.1044 ± SE 0.0056 (likelihood test P < 0.0001), i.e. an average annual increase of 11% (23 chamois year^-1). In 2002 eight chamois were observed in the Lakartxela massif, indicating an extension of the western limit of the subspecies. Since then reproduction has occurred annually and the estimate of the minimum population has increased slightly: 2003 (5 chamois), 2004 (8), 2005 (7), 2006 (10) and 2007 (11).

Fig. 2

Number of chamois observed in the massifs of Ezkaurre (1995–2006) and Larra–Lapaquiza (1996–2006), with the population trend fitted by Poisson regression (lines).

Inter-agency coordination to foster the recovery of Pyrenean chamois at the western limit of its range resulted in a significant recovery of the population and an increase in its area of distribution. The protected area of Larra–Belagoa Nature Reserve, which does not permit hunting, and the neighbouring area of Los Valles Game Reserve, where hunting is strictly controlled, along with the decision to ban hunting for a prolonged period in the Game Reserve, provided the basis for the recovery of the chamois populations at Ezkaurre and Larra–Lapaquiza and the establishment of a new population in Lakartxela. Throughout the Pyrenees these types of areas have been vital for the recovery, maintenance and expansion of chamois populations, as well as for populations of wild boar, and roe and red deer (Gortázar et al., Reference Gortázar, Herrero, Villafuerte and Marco2000).

In 2006, based on the size of the chamois population, the Government of Aragon permitted hunting in the massifs that are shared with Navarre. The hunting quotas were based on 5% of the estimated minimum population size and the proportions of the total area in each of the two massifs. The coordinated management described here can be of value for the conservation of other mountain ungulates that have distributions spanning regional administration bodies.