Printer Friendly

Estrategias ecologicas e impacto del jabali en provincias fitogeograficas de Argentina con enfasis en las tierras aridas.

Ecological strategies and impact of wild boar in phytogeographic provinces of argentina with emphasis on aridlands


The wild boar (Sus scrofa) is native to Eurasia and northern Africa (Long, 2003), but now has one of the widest geographic distributions of all exotic mammals (Oliver et al., 1993). Due to the damage it causes in natural ecosystems and agricultural areas, it is considered one of the 100 most harmful invasive species of the world (Lowe et al., 2000). The wild boar is an omnivorous species with a diet dominated by plant material (between 87 and 99%) and a smaller representation of animal matter (Schley and Roper, 2003). It has a high reproductive capacity due to characteristics such as precocious sexual maturation (from 5 to 12 months), its relatively short gestation time (120 days), and large litter size (5-7 piglets) (Gethoffer et al., 2007; Herrero et al., 2008). It also has a high tolerance to different climatic conditions, reflected in its wide geographic range (Oliver et al., 1993). For all these traits, wild boar has expanded successfully to all continents except Antarctica (Long, 2003). Nowadays this species occurs in different parts of the world either in pure wild or barely-modified feral form due to its crossing with domestic pigs (Baber and Coblentz, 1986; Merino and Carpinetti, 2003).

In its native range, this species occupies different types of habitats such as forests, shrublands, mangroves, grasslands, and wetlands (Rosell et al., 2001). In spite of that, wild boar prefers those habitats that offer high energy food, such as acorns, and have high vegetation cover for protection from predators (including hunters), as well as those close to water resources (Kurz and Marchinton, 1972; Massei and Genov, 1995).

Several climatic and ecological factors have been described to affect the abundance and distribution of wild boar (Jedrzejewska et al., 1997; Acevedo et al., 2006). For example, rainfall generates an increase in the number of pregnant females during rainy years (Fernandez-Llario and Mateos-Quesada, 2005). Hunting pressure also affects its spatial behavior by modifying choice of resting sites (Scillitani et al., 2009). Heterogeneous landscapes (i.e., high diversity of food resources and high availability of shelters) also favor high densities of wild boar as compared to homogeneous habitats (Fernandez-Llario, 2004; Acevedo et al., 2006).

The wild boar is considered an ecosystem engineer due to its rooting behavior, which transforms the physical state of biotic and abiotic materials (Jones et al., 1994; Crooks, 2002). To forage, wild boars overturn extensive areas of soil, leaving them bare of vegetation (Hone, 1988). This rooting behavior creates a complex mosaic of disturbed patches of different ages and sizes (Cuevas et al., 2012). This type of activity sometimes generates benefits to native and exotic flora, such as increasing plant richness and cover of perennial grasses (Tierney and Cushman, 2006). But it also causes negative effects such as mixing soil horizons, reducing vegetative cover and litter, accelerating the leaching of ions from litter and soil (e.g., Ca, P, Zn, Cu, and Mg), increasing nitrate concentrations and soil respiration, and decreasing the abundance of soil arthropods (Singer et al., 1984; Mohr et al., 2005; Risch et al., 2010).

Here we review and summarize the literature on wild boar ecology and ecosystem impacts in different phytogeographic provinces of Argentina, identifying knowledge gaps and research priorities toward a better understanding of this invasive species in Argentina. The aims of our contribution involve an overview of scientific studies of wild boar ecology and impact in Argentina, with a particular focus in their ecological strategies to survive in semiarid conditions.

We performed searches in specialized journals and data bases (e.g. Blackwell, Elsevier, Google Scholar, Scielo and Scopus), using different combinations of the following keywords: Sus scrofa, feral pig, wild boar, ecology, feeding habits, diet, habitat use, impact, Argentina. We also reviewed doctoral and Master's theses. We set the search for studies between 1970 and 2015 and included studies referring to wild boar and feral pigs. The literature search yielded 234 studies of which 17 were relevant to the objective of this study (Table 1), from which we found 13 scientific articles, 3 doctoral theses and 1 technical report related to wild boar ecological strategies (i.e., way in which the species uses available resources in the invaded habitat, such as diet, habitat use, resource selection, that permit wild boar to survive in it) and impact on soil properties and plant species composition and structure.


The wild boar was first introduced to Argentina in 1906 in San Huberto ranch, La Pampa for hunting purposes (Daciuk, 1978). After that, wild boar reintroductions occurred several times in different parts of the country, such as in Collun-co ranch, Neuquen in 1917 and Huemul ranch, Rio Negro in 1924 (Daciuk, 1978). Furthermore, the continuous installation of hunting grounds involves the introduction of new populations of this species around the country. In a recent study, Ballari et al. (2015a) evaluated the current status of wild boar in Argentina's system of protected areas. They showed that wild boars are present in at least 10 ecoregions belonging to 8 phytogeographic provinces (High Andean, Monte Desert, Chaco, Paranaense, Pampean grassland, Espinal, Patagonian and Subantarctic provinces) (Fig. 1). While in the rest of the provinces (Puna, Prepuna, Yungas) they did not find any record of this species. They also found novel ecoregions being occupied by this species, like High Andean, Parana Flooded Savanna and Ibera Marshes, which indicates that wild boars are continuously expanding their geographic range in Argentina. Nevertheless, studies about their ecology and ecosystem impacts in different biomes of Argentina are scarce. Information is available in only four phytogeogeographic provinces: Pampean grassland, Espinal, Subantarctic region, and Monte Desert (Fig. 1, Table 1).

Pampean grassland

The climate of this province ranges from temperate to warm, having rainfall throughout the whole year that decreases from north to south and from east to west (range: 600-1100 mm rainfall annually). Dominant vegetation is grasslands with a lower presence of halophyte steppes, marginal forests, and several types of hydrophilic shrubs (Cabrera, 1971).

For this biome, there are two studies about Sus scrofa, in which area occur feral populations of domestic pigs, both in Bahia Samborombon (35[grados]26' S, 57[grados]47' W) where feral pigs were reported in 1980 (Merino and Carpinetti, 2003; Perez-Carusi et al., 2009; Ballari et al., 2015a) (Table 1). This area has an annual precipitation of 1000 mm and small patches of "tala" forest (Celtis tala) surrounded by humid and salty grasslands (Cabrera, 1971). This area has a special significance as a refuge for several native species that have disappeared in other parts of the Pampas region (Merino and Carpinetti, 2003). Between 1995 and 1998, Merino and Carpinetti (2003) assessed feral pig populations using aerial counts. They found that pig abundances showed an accelerated increase, from about 700 individuals at the beginning of the study to more than 2000 at the end, including several peaks reaching over 4000 individuals.

A second study conducted by Perez Carusi et al. (2009) used the same methodology of counting, but also compared the spatial distribution and abundance of feral pigs with the sympatric pampas deer (Ozotoceros bezoarticus celer), a native species with endangered conservation status (Ojeda et al., 2012). They reported indirect evidence of a potential negative impact of feral pigs on pampas deer: compared to previous years there was a decrease in pampas deer abundance and spatial distribution while feral pigs increased on both counts. The authors also suggested that the decrease in abundance of pampas deer could be related to other factors such as the outbreak of FMD (foot and mouth disease) and/or the effect of poaching. Still, Perez Carusi et al. (2009) found a negative correlation between abundances of pampas deer and feral pigs, but did not assess the habitat or food use of these two species. Although pampas deer is a strict herbivore and pigs are omnivorous, the bulk of feral pig diet is plant matter (90%) (Schley and Roper, 2003; Ballari and Barrios-Garcia, 2014). Further research on the niche axes (e.g., food, habitat) of these species may provide a more thorough assessment of their coexistence mechanisms.

Perez Carusi et al. (2009) observed a 400% increase of pig population during the period of study. However, this finding should be taken cautiously, because at the end of Merino and Carpinetti's (2003) study, pig population was over 2600 individuals, while in Perez Carusi et al.' (2009) study it was 2690 individuals. Still, comparing both studies, there was a substantial increase in pig density, from 1.59 ind/[km.sup.2] to 7.78 ind/[km.sup.2]. It should be noted that these studies differed in number of sighting trips and transects, and the size of surveyed area.


The Espinal phytogeographic province has a diverse climate that changes latitudinally from warm and wet in the northern part to temperate and dry in the central and southern areas. Accordingly, the vegetation also varies, showing deciduous dry forests, palm groves, grasslands, savannahs and shrub steppes (Cabrera, 1971).

The southern part of this region was home to the first introduction of wild boar in Argentina (San Huberto ranch, La Pampa province). Despite having the oldest wild boar population in the country, there is no scientific information evaluating its interactions with native species or the impact upon the invaded ecosystem. Instead, the ecology and impacts of wild boar in this region have been conducted in an area that differs markedly from the introduction site: El Palmar National Park (EPNP), Entre Rios province (31[grados]50' S, 58[grados]17' W) (Govetto, 1999; Ballari, 2013; Ballari et al., 2015b) (Table 1). The landscape is characterized by a heterogeneous mosaic of vegetation patches that includes gallery forests, shrublands, grasslands and savannahs, with Yatay palms (Butia yatay) in highlands (Movia and Menvielle, 1994). The climate is warm (annual mean temperature 28.9[grados]C) and wet throughout the year with no dry season (annual mean precipitation 1300 mm; Papadakis, 1974). Wild boars have been reported in this protected area since 1950 (Ballari et al., 2015a).

Based on stomach contents, Ballari et al. (2015b) found that 81.2% of the wild boar diet at EPNP is plant material and almost 18.8% is animal matter. They observed that during the fruiting of Yatay palm (an endemic and protected species) wild boars eat those fruits to reach approximately 50% of their diet in summer. But during winter/autumn and spring, when those fruits are not available on the ground, boar fed mainly on corn (a supplemental feeding used in EPNP for controlling the species, and to promote hunting), this item comprising between 40 and 50% of the diet. Only during spring, the bulk of the diet is corn (42%) and animal matter (27%). So, it appears that during the masting period of Yatay palm, boars prefer to eat it over the supplemental corn. The relatively high dietary content of animal matter in EPNP could be related with the ingestion of corn and fruits of Butia spp., whose species are high in carbohydrates but low in protein (Schley and Roper, 2003; Hoffman et al., 2014). So their gain of caloric requirement from corn may cause wild boar to compensate for lack of protein by eating more animal matter (Schley and Roper, 2003).

Regarding habitat use, Govetto (1999) found a high density of wild boar signs in Yatay palm forest during the masting period (February and March), and also Ballari (2013) found that wild boar prefers habitats with a dominant tree canopy, e.g., Yatay palm forest and forest of exotic xerophytes (white cedar Melia azedarach, Gigg's firethorn Pyracantha atalantoides, honey locust Gleditsia triacanthos, broad-leaf privet Ligustrum lucidum, Chinese privet Ligustrum sinense). Agricultural lands that surround the park were not preferred by wild boars, possibly due to abundant food resources present in the park, including the supplemental feeding (corn) for hunting practices (Ballari et al., 2015b).


The climate of this phytogeographic region is temperate and wet with mean temperature 9.5[grados]C in the northern portion and 5.4[grados]C in the south. Annual precipitation goes from 2000 mm on the west bordering with Chile to 750 mm to the east of this region. Dominant vegetation types are pure or mixed forests of conifers like cordilleran cypress (Austrocedrus chilensis, Fam. Cupressaceae) and alerce (Fitzroya cupressoides, Fam. Cupressaceae), evergreen species like coihue (Nothofagus dombeyi, Fam. Nothofagaceae), and deciduous species of southern beech such as nire (N. antarctica, Fam. Nothofagaceae) and lenga (N. pumilio, Fam. Nothofagaceae). These forests are mixed to a lesser extent with grasslands and peatlands (Cabrera, 1971). Wild boars have been introduced to Patagonian forest since 1917 (Daciuk, 1978).

Within this region, wild boar studies have focused on habitat use, distribution range and impact on soil properties and vegetation (Pescador et al., 2009; Sanguinetti and Kitsberger, 2010; Schiaffini and Vila, 2012; Barrios-Garcia, 2012; Barrios-Garcia and Simberloff, 2013; Barrios-Garcia et al., 2014; Gantchoff and Belant, 2015) (Table 1).

Regarding habitat use, Schiaffini and Vila (2012) registered the presence of wild boar signs through transects along an altitudinal gradient (from 300 to 1200 m elevation) at Los Alerces National Park (LANP, 42[grados]50' S, 71[grados]52' W). They found that between 600 and 700 m there was the highest abundance of wild boar signs and that at elevation 1200 m there was no evidence of its presence. Nothofagus dombeyi and N. antarctica forests were used by this species more than forests of N. pumilio and grasslands. The authors concluded that the increased presence of wild boar in intermediate elevations was associated with the dense understory vegetation of Nothofagus forests, which provides warmth and moisture conditions that boars need to meet thermal requirements. Also, the high canopy (40 m) provides shelter from hot summer temperatures (~30[grados]C). Further, the dense understory of bamboo (Chusquea culeou) affords protection from frost during cold days, allowing boars to find food under it.

Gantchoff and Belant (2015) evaluated the influence of environmental and anthropogenic factors on wild boar occurrence in a tourist site of Nahuel Huapi National Park (NHNP, 40[grados]57' S, 71[grados]33' W) using camera traps. Similarly as in Schiaffini and Vila's (2012) study, they found that wild boar frequently uses Nothofagus dombeyi and N. antarctica forests compared with N. pumilio forests. They found that longer distance to human settlements and closer distances to roads were the most important anthropogenic variables influencing the occurrence of wild boar in the park. That result plus the boars' nocturnal activity indicates that boars use roads as corridors to move across forests while avoiding human due to hunting pressure (Gantchoff and Belant, 2015).

Regarding distribution range, Pescador et al. (2009) assessed the presence and the relative abundance of wild boar in 1985 and then repeated it in 2005 along transects in Lanin National Park (LNP, 39[grados]34'S, 71[grados]27'W). They found that after 20 years wild boar increased its range with a spread rate of 3500 ha per year.

Studies about impact of wild boar on vegetation structure, seed predation, and soil properties were recently conducted in LNP and NHNP. At NHNP, Barrios-Garcia et al. (2014) studied the impact of wild boar on vegetation and soil properties through an enclosure experiment in three different plant communities: Austrocedrus chilensis, Nothofagus dombeyi and shrublands. Results showed that wild boar rooting generates a 60% reduction in aerial plant biomass, this negative effect being stronger in Nothofagus forests. Cover of herbs and grasses was lower in rooting patches, herb cover being least in Austrocedrus and Nothofagus forests while grass cover was also lower in Nothofagus forest. Shrub cover was also negatively affected by rooting, but it was in shrubland that the authors noticed the major impact. Regarding litter decomposition rate, this was lower in rooting patches. At soil level, wild boar rooting only modified soil compaction, making this attribute lower in both forests (Table 2). Finally, the authors concluded that impact caused by wild boar is greater aboveground than belowground.

In a second enclosure experiment BarriosGarcia and Simberloff (2013) evaluated the effect of rooting on non-native seedling establishment and plant growth, and wild boar's role in seed dispersal of native and exotic plant species. Rooting patches showed higher non-native seedlings and biomass of seedlings, biomass being greatest in shrublands. All exotic plant species except for sweet brier (Rosa rubiginosa) and elmleaf blackberry (Rubus ulmifolius) showed higher establishment in rooting patches. The authors also found that both soil samples and feces showed equal composition of seed species, but in fecal samples there were fewer non-native species of seed compared with soil samples. Lastly, they found a positive effect (invasional meltdown) in the establishment of non-native seedlings in rooting patches and a negative effect in non-native seed dispersal.

Sanguinetti and Kitzberger (2010) evaluated the impact of wild boar on seed survival and seedling establishment of Araucaria araucana in LNP through an experiment at different distances from a female tree of araucaria. The authors observed that wild boars preferred mixed A. araucaria-N. pumilio over A. araucaria-N. antarctica forests for feeding. They found that wild boar consumed between 10 and 30% of available seeds. Predation was greater in places with low plant cover and close to seeding trees. When they excluded wild boars, they found that the number of surviving seeds increased, resulting in higher seedling establishment during non-masting years (boars ate proportionally more seeds during such periods than during masting). Finally, the negative effect of wild boar was reflected at individual tree level, but not at population scale.

To sum up, wild boars in the Subantarctic region more often use Nothofagus forests and those habitats are the most affected by rooting behavior. The disturbance by wild boar affects properties not only at community level but also at ecosystem scale, changing plant community composition and structure, decreasing decomposition rates, and promoting invasive plant establishment and growth.

Monte Desert

Aridlands are one of the most extensive terrestrial habitats on the planet, occupying about a third of the Earth's surface. Aridlands are characterized by high temperatures, water deficit and low plant productivity, generating a great challenge to the survival of plants and animals in these environments (Cloudsley-Thompson, 1975; Brown et al., 1979; Polis, 1995).

South American aridlands have played an important role in the evolution of the temperate biota of the continent, with high biological diversity that contains a large percentage of endemic genera and families (Ojeda et al., 1998). In Argentina, aridlands are undergoing rapid habitat conversion as a result of human activities (agriculture, grazing, logging, etc.), desertification, and salinization (Ojeda and Mares, 1982). To these challenges, environmental changes driven by climate change are added, as well as changes caused by invasive species (Boulanger et al., 2007; Cuevas et al., 2012). Considering that the temperate biomes of Argentina concentrate the highest numbers of invasive mammals of South America (Ojeda et al., unpublished data), the study of invasive species in the process of expansion is an interesting opportunity to assess the conditions and constraints that these species face within the dynamics of aridland invasibility.

In Argentina, 57% of the territory consists of aridlands (Verbistk et al., 2010). Overall, there are 23 exotic species of mammals (including feral populations of domestic species), with at least six of them found in this region: wild boar (Sus scrofa), European rabbit (Oryctolagus cuniculus), European hare (Lepus europaeus), blackbuck (Antilope cervicapra), donkey (Equus asinus), red deer (Cervus elaphus) (Novillo and Ojeda, 2008).

Monte Desert is a subtropical to warm temperate desert and semidesert located in western Argentina (Abraham et al., 2009) (Fig. 1). The climate is dry and warm in the northern portion and dry and cold in southern part of this phytogeographic province. The precipitation varies between 80 and 250 annual mm, and temperature from 48[grados]C to -17[grados]C (Labraga and Villalba, 2009). Dominant vegetation types are shrubland steppes of xerophytes, psammophytes or halophytes, as well as marginal Prosopis woodlands (Cabrera, 1971).

In this region, wild boar has been studied from a great variety of aspects, including habitat use, diet, climatic influence, and impacts on vegetation composition and on physical, chemical and microbiological soil properties (Campos and Ojeda, 1997; Cuevas et al., 2010; Cuevas, 2012; Cuevas et al., 2012; Cuevas et al., 2013a; 2013b) (Table 1). Although wild boar is not physiologically adapted to arid environments (Baber and Coblentz, 1986), they have successfully colonized them worldwide, such as in the deserts of USA, Australia, and Argentina (Barrett, 1978; Saunders and Giles, 1995; Cuevas et al., 2010). For that reason, studies that help us understand the ecological strategies that boars use in environments quite different from their native range may yield insights about the traits and factors that constraint or facilitate the expansion of invasive species.

Wild boar studies within this phytogeographic region have been conducted in the Man and Biosphere (MaB) Reserve of Nacunan (34[grados]02' S, 67[grados]58' W), Mendoza province. The landscape is characterized by a heterogeneous mosaic of vegetation patches. Dominant habitats are Prosopis woodland or algarrobal (Prosopis flexuosa, Fam. Fabaceae), Larrea shrubland or jarillal (Larrea cuneifolia, Fam. Zygophyllaceae), and sand dunes. The climate is semiarid and strongly seasonal, with hot, humid summers and cold, dry winters. Mean annual precipitation and temperature are 326 mm and 15.6[grados]C, respectively, with a maximum annual mean of 23.8[grados]C and a minimum annual mean of 7.6[grados]C (Estrella et al., 2001; Labraga and Villalba, 2009). Wild boar was first sighted in this area in the 1980's (Cuevas et al., 2010).

Cuevas et al. (2013a) studied habitat use by wild boar through signs such as tracks and rooting. Considering tracks at the habitat level, the authors did not find any difference among the three available habitats, which means that at least for displacement (moving from one place to another) wild boars used the different habitats in proportion to their availability. Regarding rooting activity they found that wild boar positively selected Larrea shrubland and avoided Prosopis woodland. At the microhabitat level, herb cover was the most important factor affecting wild boar presence, showing a positive association between this and the abundance of signs.

Based on wild boar feces, Cuevas et al. (2013b) found that the diet consisted of 96% plant matter and 4% of animal matter. Herbs were the most frequently consumed food item (~50%) followed by woody species. Aerial parts were consumed more frequently during the dry season, whereas during the wet season, fruits and animal tissue were more frequent. Regarding trophic selection, herbs were the only food item selected by wild boars, while trees like algarrobo dulce (Prosopis fleuxosa) were consumed as available only during the wet season, which is the season where this tree species bears fruit. They also found that wild boar used food resources according to seasonal availability, observing a broader trophic niche with higher plant diversity in the wet season. Finally, the most consumed food items (fruits of Prosopis flexuosa, leaves of malvisco [Sphaeralcea miniata], and bulbs of papilla [Pitraea cuneato-ovata]) had high forage quality and high carbohydrate contents, which means immediate energy for the organism.

Cuevas et al. (2013a) found that wild boars used the habitat as a function of food availability. This is because Larrea shubland, which was the only habitat selected by boars through rooting sign (their main way of finding food), is associated with high herb cover, and herbaceous plants were the most frequent food item as well as preferred in their diet (Cuevas et al., 2010; Cuevas et al., 2013b). High carbohydrate input is considered important in the diet of an individual as it is an essential component in keeping the body in good physical condition and also for the accumulation of reserves to be used during more critical periods (food scarcity) and/or periods of highest energy demand (reproduction) (Abaigar, 1993). Furthermore, around this protected area there are no croplands so the ingestion of energy-rich food is crucial for boar survival, particularly in arid conditions where the majority of plants have high fiber content and low nutritional value (Noy-Meir, 1973). This foraging strategy enables wild boar to maximize energy budget through food selection. Besides being a generalist species (Rosell et al., 2001), in the semiarid environment of the Monte Desert the wild boar appears as a species that selects both space (habitat use) and food (herbs) (Cuevas et al., 2013a; 2013b).

Regarding climatic influences on wild boar activity at local scales, Cuevas et al. (2013a) found a positive association between the number of days with low temperature and the number of wild boar signs recorded in the Reserve. This means that the seasonal activity and/or daily movements of wild boars in periods or seasons of high temperature were reduced. Thus, temperature could be a limiting factor for wild boar activity, especially in aridlands, because boars lack sweat glands or other cooling physiological mechanisms for maintaining hydric and thermal balance. They require free water, shade, a diet rich in water, and/or a behavioral response to increased environmental temperatures (Rosell et al., 2001; Dexter, 2003). In the Monte Desert, Cuevas et al. (2013a) found that wild boars showed a behavioral response related with daily movements patterns to increased environmental temperature, but they did not find a strong association with free water.

To sum up, ecological strategies of wild boar in aridlands of Argentina where water resource is scarce and exposure to sun is high, shade could be essential for surviving. Therefore, it is necessary that wild boars minimize the exposure to high temperatures and maximize the food intake of high quality forage to maximize their energy input.

According to Campos and Ojeda (1997), wild boar causes damages by chewing nearly 100% of ingested seeds of Prosopis flexuosa. While that study was based on only 3 samples of feces, a more recent study (Cuevas, unpublished data) has observed that of a total of 1618 seeds (39 fecal samples), 30% had the entire (apparently healthy) seed coat while the remainder 70% was damaged, either by boar chewing (17.3%), bruchid insects (31.7%), or other causes (21%). Nevertheless, of all the "healthy" seeds (250), the author observed that only one had germinated after one and a half months. Future studies are needed to understand the role of wild boar in the life cycle of such a key species as Prosopis fleuoxa in the Monte Desert.

Regarding the effect of wild boar rooting, Cuevas et al. (2012) observed that disturbed patches were modified in physical, chemical and microbiological soil properties in a short-term (fresh disturbance) (Table 2). Regarding the impact on vegetation, those authors found that wild boar activity through rooting produced a decrease in plant richness and diversity, generating a negative effect on perennials such as tomillo (Acantolippia seriphioides), jarilla (Larrea cuneifola) and llaullin (Lycium sp.), and on annuals such as verbena (Glandularia mendocina), papa del quirquincho (Heliotropium mendocinum), malvisco (Sphaeralcea miniata) and llanten peludo (Plantago patagonica). These impacts could occur either by mechanical action when boars forage and many plants remain with their roots exposed, or by consumer action, because many of these species were found in the diet (Cuevas et al., 2012; Cuevas et al., 2013b). The only species that was favored by rooting was Pitraea cuneato-ovata, which is an annual native species with high water requirements that grows in waterlogged and disturbed soils (Stasi and Medero, 1983). This positive effect on P cuneato-ovata establishment could be due to the change of soil properties by wild boar.

The high C/N ratio found in disturbed soils indicated that nitrogen mineralization was faster in these soils (Cuevas et al., 2012). This could be because of the high soil moisture and oxygenation (lower compaction) found in those patches, or the incorporation of litter into the soil, which was found to be lower there (Cuevas et al., 2012). It should be pointed out that the longer the time between processes of mineralization and requirements of new vegetation, the lower the efficiency of nutrient uptake and use (Abril, 2002). So when mineral nitrogen is released during periods without vegetation, it is subjected to loss by leaching or volatilization (Abril, 2002). Thus, the high contents of mineral nitrogen found in disturbed soils could be lost due to rains, leaving the soil without the nitrogen needed for future plant growth (Cuevas et al., 2012). To sum up, Cuevas et al. (2012) concluded that the physical alteration of soil due to wild boar rooting has consequences on its chemical properties. And these new soil characteristics could be responsible for a reduced plant cover and less soil bulk density, which could increase soil degradation by wind erosion. Even though this impact is at the microsite scale, disturbance by wild boars could be another factor contributing to accelerating the desertification process in the Monte Desert (Cuevas et al., 2012).


Globally, invasive species have a significant effect on both economic and environmental systems (Vitousek et al., 1997). In many countries, economic losses due to biological invasions have been and continue to be in the millions (Pimentel et al., 2001). At an ecological level, the establishment of new species to new environments has led to major changes in community composition and ecosystem functioning, resulting in many cases in the disappearance of native species through predation, competition for resources, spread of diseases, alteration of genetic diversity, habitat destruction, increased soil erosion, changes in hydrology and nutrient cycles, disruption of soil regimes, among other effects (Brown, 1989; Mack and D'Antonio, 1998; Byers et al., 2002; Lockwood et al., 2007). The study of invasive species in invaded habitats is necessary not only as a good opportunity to address topics such as basic processes in ecology but also the invasion process, how ecosystems function, and to evaluate the effectiveness of population management plans (Sax et al., 2007).

In this review we could observe that although wild boar is an omnivorous species whose diet consists mainly of plant matter, it prefers items rich in energy such as bulbs and fruits of Pitraea cuneato-ovata, Prosopis flexuosa, Araucaria araucana, and Butia yatay. These resources represent immediate energy for boars. Hence their main food strategy, especially in arid and semi-arid ecosystems where the majority of plants have low nutritional value due to their high fiber contents (Noy-Meir, 1973). Extreme conditions in arid and semiarid environments involve seasonal and spatial variation of resources (van Horne et al., 1998) which can have significant consequences on the population dynamics of species, especially in periods of scarcity (Ostfeld and Keesing, 2000). High dietary intake of carbohydrates (e.g., in the fruits mentioned above) is expected to be compensated with high intake of protein from animal matter for proper nutrition (Schley and Roper, 2003). For that reason wild boar would be increasing the consumption of animal matter in periods of fruiting when they eat more food rich in energy (Schley and Roper, 2003). This was observed in both Espinal and Monte provinces. This strategy was also observed in places where the species is native and where it is introduced (Barrett, 1978; Abaigar, 1993; Massei et al., 1996; Schley and Roper, 2003).

Regarding the Subantarctic region, future studies evaluating wild boar feeding habits, including their seasonal variation, could help us understand why this species prefers Nothofagus forests to other types of environments. Those forests likely offer not only shelter but also food, because others studies have shown that wild boar habitat use is a function of food availability (Barrett, 1982; Welander, 2000; Cuevas et al., 2013a). Similar information on diet and habitat use of wild boar is also needed in the Pampean grassland province, where niche interactions and possible competition between this species and Pampas deer require evaluation.

The mesquite Prosopis spp. plays an important role in the organization of animal and plant communities (Mares et al., 1977). In Monte Desert, wild boar consume Prosopis flexuosa, a key species for its provision of shelter, shadow, and fruit to many native animals such as the zorro gris or South American gray fox (Lycalopex griseus), mara or patagonian hare (Dolichotis patagonum), vizcacha or plains vizcacha (Lagostomus maximus), and domestic animals such as cows and horses (Campos and Ojeda, 1997). In another study, Lynes and Campbell (2000) reported that 70% of seeds of American carob (Prosopis pallida) in the feces of wild boar germinated. Future studies on the viability and germination of seeds of Prosopis flexuosa in feces of wild boar are thus needed to understand the role of boars in the recruitment of this key tree species in Monte Desert.

In addition, the impact of wild boar upon Yatay palm requires additional investigation. Boars may serve dual roles as possible seed dispersers (they defecate whole seeds upon eating its fruit) and as predators upon Yatay seedlings, where during non-masting periods they dig around the plant, leaving their roots exposed and causing it to die (Ballari, 2013). Therefore, wild boar may in fact reduce the recruitment of Yatay palm in EPNP. Future studies about its role in the predation or dispersal of Yatay palm are crucial to determine this.

Regarding the impact of wild boar rooting behavior, we found evidence suggesting no substantial changes in soil properties in the Subantarctic region, whereas in the Monte Desert there were modifications of physical, chemical, and microbiological properties caused by rooting, and leading to wind erosion of soil. These differences in the impact of rooting may be tied to soil characteristics and resilience. While soils of Patagonian forest are derived from volcanic ashes with high capacity of stabilizing soil organic matter, buffering pH, and retaining P and water which confers high resistance to nutrient loss (Diehl et al., 2003), soils in Monte Desert have an inherent tendancy (fragility) to desertification attributable to an interaction between the system's own fragility due to aridity, erosive forces from water and wind, salinization processes, and anthropic actions such as livestock pressure, logging, and fire regime modification (Villagra et al., 2009). Therefore, soils in the Subantarctic region may be better buffered to short-term disturbances in comparison with Monte Desert soils, where the presence of a new disturbance factor (wild boar rooting) could have consequences such as increasing desertification.

As we mentioned above, temperature and the availability of free water are two important factors for wild boar population distribution and abundance. In several cases, when the temperature is high wild boars are restricted to areas of dense vegetation cover and close to water resources (Dexter, 1998; Acevedo et al., 2006). Cuevas et al. (2013a) observed that in the Monte Desert, daily movements of wild boars in periods or seasons of high temperature were reduced. Thus, at local scale, temperature could be a limiting factor in wild boar activity. At regional scale, wild boar could be also affected by temperature: in areas where temperature is low there is an increased presence of wild boar (Cuevas, unpublished data). Studies focused on movements, activity pattern, home range, and reproductive capacity in different climatic conditions are needed to understand why this species is so successful.

Regarding management strategies of wild boar in Argentina, Ballari et al. (2015a) found that 54% of the surveyed protected areas apply some control method. Hunting was the most commonly used technique of wild boar control, a method that managers of protected areas (e.g., EPNP, Islas de Santa Fe National Park, Laguna de Llancanelo Natural Wildlife Reserve and Campos del Tuyu National Park) have reported to be effective for reducing the boar population. However, the authors found that hunting and in combination with others methods--such as traps--were actually ineffective and did not reduce the abundance of this invasive species. In EPNP, the method of baiting the species with supplemental feeding (corn) could in fact have the unintended consequence that boars more frequently use the protected area, rather than the private agricultural lands that surround the park, due to the supplemental food being available the whole year. A similar situation was found in Europe, where landowners bait the wild boar to keep them in woodland areas and protect their crops (Cellina, 2008). While the current baiting strategy in EPNP benefits landowners, it appears to be detrimental to the park's objectives regarding the conservation of endemic species such as Butia yatay. Although the control method has been effective according to managers of the protected area (Ballari et al 2015a), it keeps wild boar population within the park. As was concluded by Cellina (2008) for European populations, supplemental feeding offered massively, year-round could lead to an increase in the reproductive potential of wild boars and thus contribute to an increase in their population density.

Although wild boar is recognized worldwide as an invasive species with negative effects on native flora and fauna (Lowe et al., 2000), in Argentina its management is not a priority. Its wide range in the country makes it imposible to eradicate (for logistical and economic reasons), yet it is still necessary to control it. The boar increases its geographical distribution in Argentina either by expanding its range or by the introduction of new populations for hunting (e.g. in Mendoza; Cuevas, unpublished data), or both. Thus, wild boar is still reaching new areas or localities, some of which are protected areas that involve the safeguarding of native biodiversity.

Finally, to design a management plan for wild boar, it is necessary not only to know the impact that this species generates on the environment, but also its ecological strategies in each particular area. Doing so will also allow us to better understand their potential future expansion to new areas (Simberloff et al., 2005). We conclude that the impacts of wild boar in Argentina are mostly negative, demanding interactions among different players (scientists, government officials, managers of protected areas, landownwers) to plan a strategy to control its populations, thus mitigating damage to native ecosystem and the productive systems of the country.


Special thanks to Nate Upham for assisting in the English version of the manuscript and for his comments, to Liliana Katinas for helping us with the figure and to Cecilia Scoones and Roberto Kiesling for the assistance with the common names of several herbs species.


ABAIGAR T. 1993. Regimen alimentario del jabali (Sus scrofa) en el sureste Iberico. Donana Acta Vertebrata 20:35-48.

ABRAHAM EM. 2001. Geomorfologia y suelos. Pp: 123126. In: El desierto del Monte: La reserva de Biosfera de Nacunan (S Claver and S. Roig-Junent, eds.). Mendoza, Argentina.

ABRIL A. 2002. La microbiologia del suelo: su relacion con la agricultura sustentable. Pp: 129-150. In: Agroecologia. El Camino hacia una Agricultura Sustentable (SJ Sarandon, ed.). Ediciones Cientificas Americanas. La Plata, Argentina.

ACEVEDO P, MA ESCUDERO, R MUNOZ and C GORTAZAR. 2006. Factors affecting wild boar abundance across an environmental gradient in Spain. Acta Theriologica 51(3):327-436.

BABER DW and BE COBLENTZ. 1986. Density, home range, habitat use, and reproduction in feral pigs on Santa Catalina Island. Journal of Mammalogy 67(3):512-525.

BALLARI SA. 2013. El jabali (Sus scrofa) en el Parque Nacional El Palmar, Entre Rios: uso de habitat, dieta, impactos y manejo. PhD thesis, University of Cordoba, Argentina.

BALLARI SA and MN BARRIOS-GARCIA. 2014. A review of wild boar Sus scrofa diet and factors affecting food selection in native and introduced ranges. Mammal Review 44:124-134.

BALLARI SA, MF CUEVAS, S CIRIGNOLI and AEJ VALENZUELA. 2015a. Invasive wild boar in Argentina: Using protected areas as a research platform to determine distribution, impacts and management. Biological Invasions 17(6):1595-1602.

BALLARI SA, MF CUEVAS, RA OJEDA and JL NAVARRO. 2015b. Diet of wild boar (Sus scrofa) in a protected area of Argentina: The importance of baiting. Mammal Research 60:81-87.

BARRETT RH. 1978. The feral hogs on the Dye Creek Ranch, California. Hilgardia 46(9):281-346.

BARRETT RH. 1982. Habitat preferences of feral hogs, deer, and cattle on a Sierra Foothill Range. Journal of Range Management 35(3):342-346.

BARRIOS-GARCIA MN. 2012. Multi-level impacts of introduced wild boar on Patagonian ecosystems. PhD thesis, University of Tennessee, Knoxville, USA.

BARRIOS-GARCIA MN and D SIMBERLOFF. 2013. Linking the pattern to the mechanism: How an introduced mammal facilitates plant invasions. Austral Ecology 38:884-890.

BARRIOS-GARCIA MN, AT CLASSEN and D SIMBERLOFF. 2014. Disparate responses of aboveand belowground properties to soil disturbance by an invasive mammal. Ecosphere 5:1-13.

BOULANGER JP F MARTINEZ and EC SEGURA. 2007. Projection of future climate change conditions using IPCC simulations, neural networks and Bayesian statistics. Part 2: Precipitation mean state and seasonal cycle in South America. Climatic Dynamics 28:255-271.

BROWN JH, D DAVIDSON and OJ REICHMAN. 1979. Granivory in desert ecosystems. Annual Review of Ecology and Systematics 10:210-227.

BROWN JH. 1989. Patterns, models and extents of invasions by vertebrates. Pp: 85-109. In: Biological Invasions: A Global Perspective. SCOPE 37 (JA Drake, HA Mooney, F di Castri, RH Groves, FJ Kruger, M Rejmanek and M Williamsom, eds.). John Wiley and Sons Ltd. Chichester.

BYERS JE, S REICHARD, JM RANDALL, IM PARKER, CS SMITH, WM LONSDALE, IAE ATKINSON, TR SEASTEDT, M WILLIAMSON, E CHORNESKY and D HAYES. 2002. Directing research to reduce the impacts of nonindigenous species. Conservation Biology 16(3):630-640.

CABRERA AL. 1971. Fitogeografia de la Republica Argentina. Boletin de la Sociedad Argentina de Botanica 14:1-42.

CAMPOS CM and RA OJEDA. 1997. Dispersal and germination of Prosopis flexuosa (Fabaceae) seeds by desert mammals in Argentina. Journal of Arid Environments 35:707-714.

CELLINA S. 2008. Effects of supplemental feeding on the body condition and reproductive state of wild boar Sus scrofa in Luxembourg. PhD thesis, University of Sussex, UK.

CLOUDSLEY-THOMPSON JL. 1975. The desert as a habitat. Pp: 1-14. In: Rodents in desert environments (I Prakash and PK Ghosh, eds.) Dr. W. Junk b.v. Publishers The Hague.

CROOKS JA. 2002. Characterizing ecosystem-level consequences of biological invasions: The role of ecosystem engineers. Oikos 97:153-166.

CUEVAS MF, A NOVILLO, C CAMPOS, MA DACAR and RA OJEDA. 2010. Food habits and impact of rooting behaviour of the invasive wild boar, Sus scrofa, in a protected area of the Monte Desert, Argentina. Journal of Arid Environments 74:1582-1585.

CUEVAS MF, RA OJEDA and FM JAKSIC. 2012. Effects of wild boar disturbance on vegetation and soil properties in the Monte Desert, Argentina. Mammalian Biology 77:299-306.

CUEVAS MF. 2012. Ecologia del jabali (Sus scrofa) en el Desierto del Monte central, Argentina. PhD thesis, University of Rio Cuarto, Argentina.

CUEVAS MF, RA OJEDA and FM JAKSIC. 2013a. Multi-scale patterns of habitat use by wild boar in the Monte Desert of Argentina. Basic and Applied Ecology 14:320-328.

CUEVAS MF, RA OJEDA, MA DACAR and FM JAKSIC. 2013b. Seasonal variation in feeding habits and diet selection by wild boars in a semi-arid environment of Argentina. Acta Theriologica 58:63-72.

DACIUK J. 1978. Estado actual de las especies de mamiferos introducidos en la Subregion Araucana (Rep. Argentina) y grado de coaccion ejercido en algunos ecosistemas surcordilleranos. Anales de Parques Nacionales 14:105-130.

DANELL K, R BERGSTROM, P DUNCAN and J PASTOR. 2006. Large herbivore ecology, ecosystem dynamics and conservation. Cambridge University Press, UK.

DEXTER N. 1998. The influence of pasture distribution and temperature on habitat selection by feral pigs in a semi-arid environment. Wildlife Research 25:547-549.

DEXTER N. 2003. The influence of pasture distribution, and temperature on adult body weight of feral pigs in a semi-arid environment. Wildlife Research 30:75-79.

DIEHL P, MJ MAZZARINO, F FUNES, S FONTENLA, M GOBBI and J FERRARI. 2003. Nutrient conservation strategies in native Andean-Patagonian forests. Journal of Vegetation Science 14:63-70.

ESTRELLA H, J BOSHOVEN and M TOGNELLI. 2001. Caracteristicas del clima regional y de la Reserva de Nacunan. Pp: 25-33. In: El desierto del Monte: La Reserva de Biosfera de Nacunan (S Claver and S Roig-Junent, eds). IADIZA, MAB, UNESCO. Ed. Triunfar. Argentina.

FERNANDEZ-LLARIO P 2004. Environmental correlates of nest site selection by wild boar Sus scrofa. Acta Theriologica 49(3):383-392.

FERNANDEZ-LLARIO P and P MATEOS-QUESADA. 2005. Influence of rainfall on the breeding biology of wild boar (Sus scrofa) in a Mediterranean ecosystem. Folia Zoologica 54(3):240-248.

GANTCHOFF MG and JL BELANT. 2015. Anthropogenic and environmental effects on invasive mammal distribution in northern Patagonia, Argentina. Mammalian Biology 80:54-58.

GETHOFFER F, G SODEIKAT and K POHLMEYER. 2007. Reproductive parameters of wild boar (Sus scrofa) in three different parts of Germany. European Journal of Wildlife Research 53:287-297.

GOVETO L. 1999. Manejo adaptativo de las poblaciones de jabalies en las areas protegidas. Administracion de Parques Nacionales. Technical report.

HERRERO J, A GARCIA-SERRANO and R GARCIA-GONZALEZ. 2008. Reproductive and demographic parameters in two Iberian wild boar Sus scrofa populations. Acta Theriologica 53(4):355-364.

HOFFMANN JF, RL BARBIERI, CV ROMBALDI and FC CHAVES. 2014. Butia spp. (Arecaceae): An overview. Scientia Horticulturae 179:122-131.

HONE JIM. 1988. Feral pig rooting in a mountain forest and woodland: Distribution, abundance and relationships with environmental variables. Australian Journal of Ecology 13(4):393-400.

JEDRZEJEWSKA B, W JEDRZEJEWSKI, AN BUNEVICH, L MILKOWSKI and ZA KRASINSKI. 1997. Factors shaping population densities and increase rates of ungulates in Bialowieza Primeval Forest (Poland and Belarus) in the 19th and 20th centuries. Acta Theriologica 42(4):399-451.

JONES CG, JH LAWTON and M SHACHAK. 1994. Organisms as ecosystem engineers. OIKOS 69:373-386.

KATINAS L, DG GUTIERREZ, MA GROSSI and JV CRISCI. 2007. Panorama de la familia Asteraceae (=Compositae) en la Republica Argentina. Boletin de la Sociedad Argentina de Botanica 42:113-129.

KURZ JC and RL MARCHINTON. 1972. Radiotelemetry studies of feral hogs in South Carolina. The Journal of Wildlife Management 36:1240-1248.

LABRAGA JC and R VILLALBA. 2009. Climate in the Monte Desert: Past trends, present conditions and future projections. Journal of Arid Environments 73:154-163.

LOCKWOOD JL, MF HOOPES and MP MARCHETTI. 2007. Invasion Ecology. Blackwell Publishing, Oxford. 304 pp.

LONG JL. 2003. Introduced mammals of the world: Their history, distribution and influence. CABI Publishing, United Kingdom. CSIRO Publishing, Australia.

LOWE S, M BROWNE, S BOUDJELAS and M DE POORTER. 2000. 100 of the World's worst invasive alien species: A selection from the Global Invasive Species Database. Published by The Invasive Species Specialist Group (ISSG) a specialist group of the Species Survival Commission (SSC) of the World Conservation Union (IUCN).

LYNES BC and SD CAMPBELL. 2000. Germination and viability of mesquite (Prosopis pallida) seed following ingestion and excretion by feral pigs (Sus scrofa). Tropical Grasslands 34:125-128.

MACK MC and CM D'ANTONIO. 1998. Impacts of biological invasions on disturbance regimes. Trends in Ecology and Evolution 13(5):195-198.

MARES MA, FA ENDERS, JM KINGSOLVER, JL NEFF and BB SIMPSON. 1977. Prosopis as a niche component. Pp: 123-149. In: Mesquite: its biology in two desert ecosystems (BB Simpson, ed.). Dowden, Hutchinson & Ross, Inc. Pennsylvania.

MASSEI G and PV GENOV. 1995. Preliminary analysis of food availability and habitat use by the wild boar in a Mediterranean area. Ibex J.M.E. 3:168-170.

MASSEI G, PV GENOV and BW STAINES. 1996. Diet, food availability and reproduction of wild boar in a Mediterranean coastal area. Acta Theriologica 41:307-320.

MERINO ML and BN CARPINETTI. 2003. Feral pig Sus scrofa population estimates in Bahia Samborombon Conservation Area, Buenos Aires province, Argentina. Mastozoologia Neotropical 10(2):269-275.

MOHR D, LW COHNSTAEDT and W TOPP. 2005. wild boar and red deer affect soil nutrients and soil biota in steep oak stands of the Eifel. Soil Biology and Biochemistry 37:693-700.

MORELLO J. 1958. La provincia fitogeografica del Monte. Opera Lilloana.

MOVIA C and MF MENVIELLE. 1994. Mapa de vegetacion del P.N. El Palmar. In: Plan de Manejo del P.N. El Palmar. Administracion de Parques Nacionales. Argentina.

NOVILLO A and RA OJEDA. 2008. The exotic mammals of Argentina. Biological Invasions 10:1333-1344.

NOY-MEIR I. 1973. Desert ecosystems: Environment and producers. Annual Review of Ecology and Systematics 4:25-51.

OJEDA RA and MA MARES. 1982. Conservation of South American mammals: Argentina as a paradigm. In: Mammalian Biology in South America. Pymatuning Symposia in Ecology 6:505-521.

OJEDA RA, CM CAMPOS, JM GONNET, CE BORGHI and VG ROIG. 1998. The MaB Reserve of Nacunan, Argentina: Its role in understanding the Monte Desert biome. Journal of Arid Environments 39:299-313.

OJEDA RA, V CHILLO and G DIAZ. 2012. Libro Rojo de Mamiferos Amenazados de la Argentina. SAREM, Argentina.

OLIVER WLR, IL BRISBIN Jr. and S TAKAHASHI. 1993. The Eurasian Wild pig (Sus scrofa). Pp: 112-121, in: Pigs, Peccaries and Hippos. Status Survey and conservation Action Plan (WLR Oliver, ed.). IUCN/ SSC Pigs and Peccaries Specialist Group and IUCN/ SSC Hippo Specialist Group.

OSTFELD RS and F KEESING. 2000. Pulsed resources and community dynamics of consumers in terrestrial ecosystems. Trends in Ecology and Evolution 15:232-237.

PAPADAKIS J. 1974. Ecologia y posibilidades agropecuarias de las provincias argentinas. Enciclopedia Argentina de Agricultura y Ganaderia 2:1-86.

PEREZ CARUSI LC, MS BEADE, F MINARRO, AR VILA, M GIMENEZ-DIXON and DN BILENCA. 2009. Relaciones espaciales y numericas entre venados de las pampas (Ozotoceros bezoarticus celer) y chanchos cimarrones (Sus scrofa) en el Refugio de Vida Silvestre Bahia Samborombon, Argentina. Ecologia austral 19:63-71.

PESCADOR M, J SANGUINETTI, H PASTORE and S PERIS. 2009. Expansion of the introduced wild boar (Sus scrofa) in the Andean region, Argentinean Patagonia. Galemys 21:121-132.

PIMENTEL D, S McNAIR, J JANECKA, J WIGHTMAN, C SIMMONDS, C O'CONNELL, E WONG, L RUSSEL, J ZEM, T AQUINO and T TSOMONDO. 2001. Economic and environmental threats of alien plant, animal, and microbe invasions. Agriculture, Ecosystems and Environment 84:1-20.

POLIS GA. 1995. Desert communities: an overview of patterns and processes. Pp: 1-26. In: The ecology of desert communities (GA Polis, ed.). University of Arizona, Arizona, USA.

RISCH AC, S WIRTHNER, MD BUSSE, DS PAGEDUMROESE and M SCHUTZ. 2010. Grubbing by wild boar (Sus scrofa) and its impact on hardwood forest soil CO2 emissions in Switzerland. Oecologia 164:773-784.

ROSELL C, P FERNANDEZ-LLARIO and J HERRERO. 2001. El Jabali (Sus scrofa Linnaeus, 1758). Galemys 13(2):1-25.

SANGUINETTI J and T KITZBERGER. 2010. Factors controlling seed predation by rodents and non-native Sus scrofa in Araucaria araucana forests: Potential effects on seedling establishment. Biological Invasions 12:689-706.

SAUNDERS G and J GILES. 1995. Ecological comparison of two wild pig populations in semi-arid and sub-alpine Autralia. Ibex J.M.E. 3:152-155.

SAX DF, JJ STACHOWICZ, JH BROWN, JF BRUNO, MN DAWSON, SD GAINES, RK GROSBERG, A HASTINGS, RD HOLT, MM MAYFIELD, MI O'CONNOR and WR RICE. 2007. Ecological and evolutionary insights from species invasions. Trends in Ecology and Evolution 22(9):465-471.

SCHIAFFINI MI and AR VILA. 2012. Habitat use of the wild boar, Sus scrofa Linnaeus 1758, in Los Alerces National Park, Argentina. Studies on Neotropical Fauna and Environment 47:11-17.

SCHLEY L and TJ ROPER. 2003. Diet of wild boar, Sus scrofa, in Western Europe, with particular reference to consumption of agricultural crops. Mammal Review 33:43-56.

SCILLITANI L, A MONACO and S TOSO. 2009. Do intensive drive hunts affect wild boar (Sus scrofa) spatial behaviour in Italy? Some evidences and management implications. European Journal of Wildlife Research 56(3):307-318.

SIMBERLOFF D, I PARKER and PN WINDLE. 2005. Introduced species policy, management, and future research needs. Frontiers in Ecology and the Environment 3(1):12-20.

SINGER FJ, WT SWANK and EEC CLEBSCH. 1984. Effects of Wild pig rooting in a deciduous forest. Journal of Wildlife Management 48(2):464-473.

STASI CR and MN MEDERO. 1983. Estudio ecologico y bromatologico de Pitraea cuneato-ovata (Cav.) Caro, una especie forrajera del Monte mendocino y sanjuanino. Deserta 7:7-11.

TIERNEY TA and JH CUSHMAN. 2006. Temporal changes in native and exotic vegetation and soil characteristics following disturbances by feral pigs in a California grassland. Biological Invasions 8:1073-1089.

VAN HORNE B, RL SCHOOLEY and PB SHARPE. 1998. Influence of habitat, age, and drought on the diet of Townsend's ground squirrels. Journal of Mammalogy 79:521-537.

VERBIST K, F SANTIBANEZ, D GABRIELS and G SOTO. 2010. Atlas de zonas aridas de America Latina y El Caribe. CAZALAC. Documentos Tecnicos del PHILAC numero 25, UNESCO.

VILLAGRA PE, GE DEFOSSE, HF Del VALLE, S TABENI, M ROSTAGNO, E CESCA and E ABRAHAM. 2009. Land use and disturbance effects on the dynamics of natural ecosystems of the Monte Desert: Implications for their management. Journal of Arid Environments 73:202-211.

VITOUSEK P, C D'ANTONIO, L LOOPE, M REJMANEK and R WESTBROOKS. 1997. Introduced species: a significant component of human-caused global change. New Zealand Journal of Ecology 21: 1-16.

WELANDER J. 2000. Spatial and temporal dynamics of wild boar (Sus scrofa) rooting in a mosaic landscape. Journal of Zoology 252:263-271.

M. Fernanda Cuevas (1), Ricardo A. Ojeda (1) and Fabian M. Jaksic (2)

(1) Grupo de Investigaciones de la Biodiversidad (GiB), IADIZA, CCT Mendoza CONICET, CC 507, 5500 Mendoza, Argentina. [Correspondence: <>].

(2) Centro de Ecologia Aplicada y Sustentabilidad (CAPES), Pontificia Universidad Catolica de Chile, Casilla 114-D, Santiago, Chile

Recibido 17 julio 2015. Aceptado 10 marzo 2016. Editor invitado: RA Ojeda

Leyenda: Fig. 1. Argentine phytogeographic provinces showing the presence of wild boar (white circles). Numbers indicate provinces with ecological and ecosystem impact information of the species. Map extracted from Katinas et al., 2007.
Table 1
Summary of wild boar studies in the phytogeographic provinces
of Argentina.

Phytogeographic                      Ecological
province              Impact           traits           References

Pampean           Potential         Population      Merino and
grassland         impact on         abundance       Carpinetti (2003);
                  Pampas deer                       Perez Carusi et
                  (Ozo toceros                      al. (2009)

Espinal           Seed predation    Diet, habitat   Govetto (1999);
                  of Butia yatay    use             Ballari (2013);
                                                    Ballari et al.

                                    Habitat use,    Schiaffini and
                                    distribution    Vila (2012);
                                    range           Gantchoff and
                                    expansion       Belant (2015);
                                                    Pescador et al.

Subantarctic      Impact on                         Barrios-Garcia
                  vegetation and                    (2012); Barrios-
                  soil properties                   Garcia and
                                                    Simberloff (2013);
                                                    Barrios-Garcia et
                                                    al. (2014)

                  Seed predation                    Sanguinetti and
                  of Araucaria                      Kitsberger (2010)

Monte Desert      Impact on                         Cuevas et al.
                  vegetation and                    (2010); Cuevas
                  soil properties                   (2012); Cuevas et
                                                    al. (2012)

                                    Diet, habitat   Cuevas et al.
                                    use             (2013a); Cuevas et
                                                    al. (2013b)

Table 2
Effects of wild boar's rooting in soil properties in both Monte Desert
and Subantarctic phytogeographic provinces.

Soil Properties                                Monte Desert

                                      Disturbed         Undisturbed

Physical          Hardness                -                  +
                  Moisture                +                  -
                  Temperature             -                  -
                    Silt                  -                  +
                    Clay                  -                  +
                    Sand                  +                  -

Chemical          Total Nitrogen               No change
                  Mineral Nitrogen        +                  -
                  Nitrate + Nitrite       +                  -
                  N[H.sub.4]                   No change
                  Organic Carbon               No change
                  C/N ratio               +                  -
                  Organic matter               No change
                  pH                           No change
                  Total Carbon                    --
                  Extractable P                   --

Microbiological   Soil respiration        -                  +
                  Ammonifiers                  No change
                  Cellulolytics                No change
                  N fixers                     No change
                  Nitrifiers                   No change

Soil Properties                             Subantarctic Forest

                                      Disturbed         Undisturbed

Physical          Hardness                -                  +
                  Moisture                     No change
                  Temperature                  No change
                    Silt                          --
                    Clay                          --
                    Sand                          --

Chemical          Total Nitrogen               No change
                  Mineral Nitrogen             No change
                  Nitrate + Nitrite               --
                  N[H.sub.4]                      --
                  Organic Carbon                  --
                  C/N ratio                       --
                  Organic matter                  --
                  pH                           No change
                  Total Carbon                 No change
                  Extractable P                No change

Microbiological   Soil respiration             No change
                  Ammonifiers                     --
                  Cellulolytics                   --
                  N fixers                        --
                  Nitrifiers                      --
COPYRIGHT 2016 Sociedad Argentina para el Estudio de los Mamiferos
No portion of this article can be reproduced without the express written permission from the copyright holder.
Copyright 2016 Gale, Cengage Learning. All rights reserved.

Article Details
Printer friendly Cite/link Email Feedback
Author:Cuevas, M. Fernanda; Ojeda, Ricardo A.; Jaksic, Fabian M.
Publication:Mastozoologia Neotropical
Date:Dec 1, 2016
Previous Article:Ecologia, impacto y manejo del ciervo colorado (Cervus elaphus) en el noroeste de la Patagonia, Argentina.
Next Article:Mamiferos introducidos en la provincia de Neuquen: estado actual y prioridades de manejo.

Terms of use | Privacy policy | Copyright © 2018 Farlex, Inc. | Feedback | For webmasters