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Domestic dogs in Atlantic forest preserves of south-eastern Brazil: a camera-trapping study on patterns of entrance and site occupancy rates/Caes-domesticos em remanescentes de Mata Atlantica no sudeste do Brasil: padroes de entrada e de ocupacao obtidos a partir de armadilhas fotograficas.

1. Introduction

Domestic animals can impact native fauna in several ways, including increased predation (Lepczyk et al., 2004; Kays and DeWan, 2004), especially on islands (Burbidge, 1999; Anderson et al., 2006), and genetic introgression (Vila and Wayne, 1999; Adams et al., 2003), which sometimes might disturb the genetic integrity of native species (Pierpaoli et al., 2003). Disease transmission seems, however, to be the most important disturbance effect in many continental countries (Cleaveland et al., 2000; Frolich et al., 2000; Anderson et al., 2003; Hammer et al., 2004). Past studies have explored the presence of domestic dogs in wild areas or their impact on wild species (Herranz et al., 2002; Butler et al., 2004; Manor and Saltz, 2004; Anderson et al., 2006), however few studies have been conducted in Neotropical forests. These include predation on native species (Kruuk and Snell, 1981; Barnett and Rudd, 1983), potential disease transmission (Ryan et al., 2003; Fiorello et al., 2004; Deem and Emmons, 2005; McFadden et al., 2005; Fiorello et al., 2006), and social biology of free-roaming dogs (Daniels and Bekoff, 1989; Fielding and Mather, 2001). In Brazil there is some information of domestic dog impacts on native fauna (Horowitz, 1992; Lacerda, 2002; Galetti and Sazima, 2006), observation of dog attacks to other domestic animals (Oliveira and Cavalcanti, 2002; Cavalcanti, 2003), dog presence in protected areas (Alves, 2003; Srbek-Araujo and Chiarello, 2005) and potential disease transmission (Courtnay et al., 2001). However, to the best of our knowledge this is the first in-depth study focused on the quantification of domestic dog presence in a conservation unit located in the Atlantic forest area. The Atlantic forest is one of the richest and most threatened forest biomes in the world (Myers et al., 2000). The degree of threat is rooted in five centuries of development, which has been greatly accelerated in the last 150 years (Dean, 1995). Today, about 70% of the Brazilian population (about 100 million people) lives within the original area of this biome, including world megalopolis like Sao Paulo and Rio de Janeiro (Galindo-Leal and Camara, 2003). As the urban areas spread, the contact of domestic animals with wild animals increases and so does the potential for disease transmission, predation and possible competition with native animals. Here we analyzed data on frequency of records, number of individuals, the spatial and temporal patterns of records and the interaction between native mammals and dogs, in a little-disturbed and well-preserved Atlantic forest reserve in south-eastern Brazil. These data are important to better assess the potential impact of dogs on Neotropical mammals, and are also important for planning management strategies of conservation units located in an increasingly urban environment.

2. Methods

2.1. Study area

The study was carried out in the 440 ha Santa Lucia Biological Station (SLBS; 19[degrees] 57' 10''-19[degrees] 59' 00'' S and 40[degrees] 31' 30''-40[degrees] 32' 25'' W), located 6 km from the urban center of Santa Teresa city (Figures 1 and 2). Santa Teresa is a small town with circa 20,000 inhabitants, the most part of which inhabit the rural area. With adjoining private land, the area of native forest in which SLBS is located totals circa 900 ha (Figures 1 and 2). Altitudes vary from 550 to 950 m (Mendes and Padovan, 2000). The weather is predominantly Cfa in Koppen's classification, being characterized by a hot and wet season (October-March) and a dry and cold season (April-September); average precipitation is 1,868 mm and average annual temperature is 19.9 [degrees] (Mendes and Padovan, 2000). Predominant vegetation is dense ombrophilous (wet) Forest (IBGE, 1993). Native forest remnants (north and west), agriculture (mainly coffee) and Eucalyptus plantations (south and east) are the predominant vegetation surrounding SLBS. A small number of rural residences are found neighboring SLBS, especially in the south and east areas. Due to high levels of species richness and endemism, this region is considered of extreme biological importance for the conservation of the Atlantic Forest (Conservation International, 2000). The non-volant mammal fauna of SLBS is rich, with 21 families and 51 species already confirmed and actually present in the reserve (Passamani et al., 2000; Srbek-Araujo and Chiarello, 2005). Other faunal groups and the flora are similarly diverse (Thomaz and Monteiro, 1997; Brown Jr. and Freitas, 2000). Further information about SBLS and region is found in Thomaz and Monteiro (1997) and Mendes and Padovan (2000).

2.2. Data collection

The study was based on camera-trapping in SLBS from February 2002 to February 2004. In a previous study, the camera data were used to discuss mammal diversity in this reserve and compare the efficiency of this technique to more traditional inventory methods (Srbek-Araujo and Chiarello, 2005). Throughout the monitoring, three camera traps of the model Wildlife Pro Camera, made by Forest Suppliers Inc. (USA), and four camera traps of the model Deer Cam--Scouting Camera, made by Non Typical Inc. (USA), were used. Both brands of equipment use 35 mm automatic cameras with passive infrared sensors that detected motion and variations of heat in a detection cone beginning at the camera. Negative 200 ASA films of 36 exposures were used. The interval between photos was set to minimum (20 and 30 seconds for the first and second brands, respectively) and cameras operated 24 hours throughout the study. Camera traps were installed in tree trunks ca 45 cm from the ground, preferably along trails and in margins of small creeks. The cameras were checked every 15-30 days for maintenance, changing of films and battery if necessary. No baits were used since these could influence natural behavior of dogs and native mammal species (Cutler and Swann, 1999).

Sampling period encompassed 25 occasions of approximately 30 days each from February 2002 to February 2004. From December 2002 to November 2003 camera traps were installed in pairs (two units at each sampling location, allowing recording both sides of a pictured mammal). In all other periods they were installed singly. A total of 28 sampling points distributed in 12 trails were sampled, with a minimum distance of 300 m between each other. The area sampled by camera traps, calculated using the minimum convex polygon method (without any buffer) totaled 157.8 ha. Given malfunctioning equipment throughout the study, the number of sampling points varied from two to three/month (see below). Further details are found in Srbek-Araujo and Chiarello (2005). Additionally, visits were carried out in rural residences located nearby SLBS (Penha, Valsugana Velha and Santa Lucia districts) aiming to locate and identify the residence of domestic dogs photographed by the camera traps inside the reserve. When this was possible, the residence-to-sampling point distance (straight line distance) was measured using a GPS (Garmin Etrex) instrument. To help find the residences of domestic dogs, one of us (ACSA) participated in a field campaign of vaccination against rabies carried out by the Environmental Surveillance Department of the Santa Teresa municipality (Setor de Vigilancia Ambiental em Saude--SVAS) in November 2003. Several residences of the rural area were visited during this campaign. The distance between the sampling point where a given dog was photographed inside SLBS and the nearest forest edge was also measured using the GPS.


2.3. Data analysis

We calculated two types of records, depending on the analysis. For analysis on inter-specific comparisons we considered the area covered by camera traps as the sampling unit and only one record per species per day was included (heretofore record type 1). This approach was judged necessary due to the small distance between adjacent sampling points (300 m), which cannot be considered as statistically independent one from another, and also due to the relatively small size of sampled area (157.8 ha). Further, given that the number of camera traps effectively functioning varied from month to month, we used record rates (number of type 1 records/camera trap-days) instead of number of records. The type 1 record, being restrictive, diminishes the chance of a same individual of a given species being photographed repeatedly during the sampling period, which would inflate the frequency of records (i.e., record rate) of this species in comparison to others. So the type 1 record was regarded as a less biased estimator of record rates when several species are compared (see Martins and Sanderson, 2006 for a relevant discussion on this). To check if frequency of domestic dogs in SLBS varied according to climate we used two approaches. First, we correlated the monthly record rates of domestic dogs with climate variables (monthly total of rainfall and average monthly temperature, both gauged in a weather station located in SLBS) using the Spearman rank correlation. Second, we compared differences in record rates of dogs, wild mammals and species record rates (number of species of wild mammals/camera trap-days) between dry season months (April to September) and wet season months (October to March) using the Mann-Whitney test. Further, we used backward stepwise logistic regression to investigate if the monthly presence of domestic dogs was related to corresponding record rate of wild mammals (all species pooled), or to species record rates. For this, the monthly presence (1) or absence (0) of domestic dogs in SLBS was considered the dependent binary variable, and four independent variables were tested: 1) monthly record rates of wild mammals, 2) monthly species record rates of wild mammals, 3) monthly total of rainfall and 4) average monthly temperature. Default settings of SPSS were used for variable selection and model fitting.


To analyze the activity period, identify individual dogs and investigate the spatial and temporal patterns of domestic dog records in the reserve we used a second record type (heretofore record type 2). This record was defined as a picture of dog taken at less than five-minute intervals in the same camera trap point (when >1 record was taken within 5 minutes, only one record was considered). The counting of records when cameras were placed in pairs was done disregarding simultaneous records taken (for each pair of simultaneous records, only one record was counted). For these periods, each pair of camera traps was considered a single sampling unit. When more than one individual of a given species was captured in a picture, only one record of the species was counted. Type 2 records were classified into nocturnal, diurnal and crepuscular using the software Earthsun version 4.6 (W. Scott Thoman, 830 Panel Road, Macedon, New York, USA). This program uses data on coordinates, date and altitude, to calculate the exact time of sunrise, sunset, start and end of twilight for each sampling day. All analyses, variable selection and model fitting were performed using the default settings of the SPSS software, version 8.0. Mammal taxonomy follows the most recent edition of Wilson and Reeder (2005).

3. Results

The 25 months of monitoring in SLBS resulted in a sampling effort of 2,142 camera-days. This effort totaled 292 (type 1) records of 21 species of native mammals, plus two other unidentified species (one small rodent and one marsupial) (Table 1; see also Srbek-Araujo and Chiarello, 2005). A total of 25 (type 1) or 36 (type 2) records of 16 domestic dogs (Canis lupus familiaris) were obtained. In two records we were unable to identify the individual dog (only part of the animal was photographed). Overall, the domestic dog was the fourth species in number of records and the top ranking among nine species of Carnivora, closely ahead of the ocelot (Leopardus pardalis), with 24 records (type 1). Only six species were recorded in >40% of sampled months, and the domestic dog was among these, with an average record rate of 1/month (range 0-8 records/month).

There were no significant correlations between climate variables and record rates (type 1) of dogs (rainfall: [r.sub.s] = -0.366; n = 22; p = 0.094; temperature: [r.sub.s] = -0.080; n = 21; p = 0.730), nor between climate variables and record rate of native mammals (rainfall: [r.sub.s] = 0.012; n = 22; p = 0.956; temperature: [r.sub.s] = -0.149; n = 21; p = 0.520). Monthly record rate of domestic dogs did not correlate significantly with corresponding record rates of wild mammals (n = 23) tested individually (Spearman rank correlation; p > 0.05 in all 23 cases). Logistic regression also failed to detect a significant relationship between the monthly presence of domestic dogs in SLBS and the corresponding record rate (type 1) of native mammals [Cox and Snell [R.sup.2] = 0.197; of the four tested independent as variables (rainfall, temperature, record rate and species record rate), only rainfall was included in the final model, but with a marginal significance (R = -0.192; p = 0.080)]. Nevertheless, direct interaction between domestic dogs and native mammal species was recorded on a single occasion: at 07:33 hours an agouti (Dasyprocta leporina) was recorded foraging on the ground in front of the camera trap and at 09:11 hours of that same day a domestic dog was photographed sniffing the exact spot were the agouti had foraged less than two hours earlier.

Regarding now the records of type 2, domestic dogs were detected in 10 of the 28 sampling points, distributed in half (n = 6) of all 12 sampled trails. The average distance between sampling points (with dog records) and nearest forest edge was 365.4 m (range = 0-1,100 m). Controlling for differences in sampling effort among sampling locations, there was a slightly higher number of domestic dog records in the two first class of distances to the nearest edge (0-399 m) (Figure 3). It was possible to determine the location of dog residence (human settlement) for only two of the 16 photographed dogs: a single house distant 668 and 948 m from the corresponding sampling points inside SLBS. No other dog photographed in SLBS was found or located during the vaccination campaign carried out in residences located nearby this reserve.

Dogs of various sizes were recorded but medium-sized ones predominated. Only one individual was young, the others were all adults or sub-adults. Both males (n = 6) and females (n = 4) were recorded (sex discrimination was possible in 62.5% of cases). Domestic dogs were photographed alone (72.2% of records) or in groups (couple of individuals; 27.8% of records) (7 different pairs were photographed). Pair formation was recorded in 10 occasions and some individuals were paired with different dogs in some occasions. Most pairs (57.1%) were composed by at least one female (all four females identified were photographed mostly in pairs). Most dogs (n = 9; 56.3%) entered the reserve in a sporadic way, being photographed only once during the study; the remaining individuals (n = 7; 43.7%) were recorded two to thirteen times each, within intervals that varied from less than one hour to eight months in between. Domestic dogs were recorded predominantly during the day (n = 32 records; 88.9%), two records were nocturnal and two during the twilight period.


4. Discussion

Our results show that a high number of records were near the reserve's border with agriculture, where rural human residences are closer (the eastern portion of SLBS). These results are in accordance with Odell and Knight (2001), which states that domestic species are detected most frequently in areas nearby human residences or places with a high density of houses. On the other hand, the western portion of SLBS, where far fewer records were obtained, is contiguous to a large tract of native forest, which therefore is likely acting as a buffer, hampering the entrance of dogs. Similarly, the occurrence of dogs in Brasilia National Park (a reserve located in Cerrado, close to the Brazilian Capital, Brasilia) was more influenced by external characteristics (dogs were seen most frequently near to developing urban and rural areas) than to internal factors of that Park, such as type of vegetation (Lacerda, 2002). So the frequent occurrence of dogs near to the borders of SLBS can be viewed as a type of edge effect (Murcia, 1995; Laurance et al., 2002), as also suggested by Lacerda (2002). The small number of individuals identified in residences near SLBS might suggest that most dogs recorded within this reserve either came from more distant areas, or are not pet dogs at all, being part of the errant (or feral) dog population of the region. Either way, an expressive number of recorded individuals (43.7%) entered this reserve repeatedly. In another Atlantic forest preserve of Brazil, Galetti and Sazima (2006) considered the study dog population as "feral", although no evidence/explanation for this categorization were detailed.

According to Manor and Saltz (2004), one of the consequences of forest fragmentation is the decreasing distance between native forest and urban zones and the consequent entrance of dogs in undisturbed areas. This is the case here. The distance between SLBS and the closest town (Santa Teresa) is short, roughly 6 km. Additionally, two thirds (68%) of the human population of Santa Teresa municipality (20,709 inhabitants; IBGE 2003) live in rural areas. Considering that most (if not all) residences located in rural areas have at least one domestic dog each (a conservative estimate), the number of dogs potentially able to enter the reserve must be very high. According to the Environmental Surveillance Department (SVAS), the domestic dog population of Santa Teresa municipality is estimated to be between 2,078 and 3,464 dogs, assuming ratios of 1:10 and 1:6 in relation to the human population, respectively (Secretaria Municipal de Saude, 2003). These results stress the need for urgent control of dog entrance in conservation units even in areas of low human population density and relatively high cover of native forests.

Although the analyses presented here failed to reveal significant relationship between domestic dogs and native mammals (i.e., potential prey), local residents and previous researchers have reported instances of dogs pursuing native mammal species such as brocket deer (Mazama spp.), armadillos (Dasypus spp., Euphractus sexcinctus, Cabassous sp.), agoutis (Dasyprocta leporina), paca (Cuniculus paca), and even primates (Callicebus personatus), suggesting that they do act as predators. Also, the comparison of record rates among species indicate that domestic dog is locally more abundant than the top terrestrial predator present in SLBS, the puma (Puma concolor), and perhaps even more so than the ocelot, a medium-sized cat. In fact, comparing stripe patterns and other external signals, seven individual ocelots and two pumas were identified in the area sampled by camera traps in SLBS, much lower figures than that of domestic dogs (16 individuals). Although the real numbers and population densities are not know, these results clearly suggest that domestic dogs might be abundant enough to potentially impact the local community of terrestrial mammals, perhaps even more so than the native terrestrial predators. In Brazil, Horowitz (1992) and Lacerda (2002) report the occurrence of dogs pursuing native mammals and the death of species due to dog attacks in Brasilia National Park, although the stomach contents analyzed (n = 18) indicated the presence of garbage, young domestic birds among other items, but no remains of native species were found (Lacerda, 2002). According to Oliveira and Cavalcanti (2002), in most attacks the domestic dog would not kill the animal or the dog would not feed on the killed prey. Similarly, Lacerda (2002) states the attacks would be related to instinctive predator-prey games rather than to hunting for obtaining food. On the other hand, the study of Galetti and Sazima (2006) lists a total of 46 carcasses of 12 species (including amphibians, reptiles, birds and specially mammals) predated by domestic dogs in Santa Genebra reserve throughout 44 months of study. But as these authors did not witness the attacks, some of the putative prey could have been scavenged rather than pre-dated.

Beside their role as predators, dogs can impact a native community also through competition. Butler et al. (2004) mention that domestic dogs are a least significant competitor of the large African predators, due to their very low ability of taking large prey. In the Neotropics, dogs could potentially compete with large cats, like jaguars (Panthera onca) and pumas (Puma concolor), and with smaller carnivores (ocelots--Leopardus pardalis, crab-eating foxes--Cerdocyon thous, among others), but data are still lacking to substantiate this. On the other hand, dogs can be preyed upon by native species (Butler et al., 2004). Farrel et al. (2000), for example, found remains of domestic dogs in puma scats in Venezuela. Although this might be considered positive as it represents a way of naturally controlling the dog population inside conservation units, it is also a mechanism of transmission of dog diseases and parasites to native mammals.

According to the Environmental Surveillance Department (SVAS) of Santa Teresa, from March 2002 to December 2003, 328 free-roaming dogs were removed from residences and public streets or roads of the municipality, most of which (68.0%) were sacrificed (the remaining returned to their owners or were adopted by others). Two important actions are enforced by this sector: disease control (Rabies and Leishmaniasis, through vaccination of healthy individuals and the sacrifice of sick dogs) and control of the free-roaming population (capture and elimination). Since the beginning of SVAS's activities, only one case of bovine rabies was confirmed in Santa Teresa (March 2003). Regarding Leishmaniasis, 15 dogs were suspected to be infected in 2002 and four in 2003 (four animals were sacrificed in the first and one in the second year, after positive confirmation via lab analysis) (Secretaria Municipal de Saude, 2003; 2004). In this sense, this program might be indirectly contributing to the preservation of native mammal species, eliminating or greatly diminishing the population of potential vectors of diseases. According to Haass et al. (1996), for example, at least eight of the 11 extant families of carnivores are susceptible to canine distemper virus. Such actions (zoonosis control) should thus be included in the list of priorities for conservation of native species, especially in contact zones such as the rural environment and areas close to conservation units (Butler et al., 2004).

Data here presented indicate that domestic or free-roaming dogs can be frequent visitors to wet tropical forests preserves of the Neotropics. Although results did not indicate a close relationship with native mammals, the abundance and temporal distribution of dog records do suggest a high potential for impact on community ecology and health of wild mammal species. It is wise, therefore to put into practice efficient measures aiming directly at the control of the canine population and the prophylaxis of diseases potentially transmitted by these animals. To be effective this control should be carried out within conservation units as well as outside them and the latter should include rural as well as urban zones. Although staff of conservation units in both the Atlantic forest and Cerrado of Brazil have to deal with this problem almost on a daily basis (pers. obs.), an integrated official agenda for domestic dog control is still to be accorded and implemented. It is equally necessary to promote the education of the human population living in cities and in rural areas, stressing the importance of keeping dogs responsibly. These animals should be well fed, vaccinated and not allowed to wander freely without being in the company, or under the control, of their owners. Although these practices are common sense in developed countries, its use and implementation in the third world is still in its infancy. Such measures will assume increasing importance as a conservation strategy, given the expected increase in human population, and the consequent increase in number of domestic animals, in most countries of the Neotropics.

Acknowledgements--We are greatly indebted to all the staff of the Museu de Biologia Professor Mello Leitao, specially its director Helio de Q. B. Fernandes and secretary Rose Loss. The Setor de Vigilancia Ambiental em Saude, especially Andre P. Fontana, kindly helped with information about the local dog population and zoonosis. Eduardo M. de Barros, Leandro S. Moreira, Luciana Barcante, Marina N. dos Santos, Oscar Echevery, Paula L. Ruiz, Pedro Amaral, Rodrigo L. Meyer, Sergio P. Costa and Valeska B. de Oliveira kindly helped with data collection. One of us (ACSA) was granted a research fellowship from the Brazilian Federal Agency CAPES. This project was funded by the Conselho Nacional de Desenvolvimento Cientifico e Tecnologico/CNPQ (grant # 469.321/2000-8) and the Fundo de Incentivo a Pesquisa--PUC Minas (grant # FIP 2002/06-TLE). AGC has a productivity grant (bolsa produtividade em pesquisa) from CNPQ (grant # 301100/2005-5).

Received February 12, 2007--Accepted August 10, 2007--Distributed November 30, 2008 (With 3 figures)


ADAMS, JR., LEONARD, JA. and WAITS, LP., 2003. Widespread occurrence of a domestic dog mitochondrial DNA haplotype in southeastern US coyotes. Mol. Ecol., vol. 12, no. 2, p. 541-546.

ALVES, LCPS., 2003. Uso de armadilhas fotograficas no levantamento da mastofauna da Reserva Biologica de Araras, IEF-RJ. Juiz de Fora: Universidade Federal de Juiz de Fora. [Bachelor dissertation].

ANDERSON, TC., FOSTER, GW. and FORRESTER, DJ., 2003. Hookworms of feral cats in Florida. Vet. Parasitol., vol. 115, no. 1, p. 19-24.

ANDERSON, CB., ROZZI, R., TORRES-MURA, JC., MCGEHEE, SM., SHERRIFFS, MF., SCHUTTLER, E. and ROSEMOND AD., 2006. Exotic vertebrate fauna in the remote and pristine sub-Antarctic Cape Horn Achipelago, Chile. Biodivers. Conserv., vol. 15, no. 10, p. 3295-3313.

BARNETT, BD. and RUDD, RL., 1983. Feral Dogs of the Galapagos Islands: Impact and Control. International Journal for the study of Animal Problem, vol. 4, no. 1, p. 44-58.

BROWN Jr., KS. and FREITAS, AVL., 2000. Diversidade de Lepidoptera em Santa Teresa, Espirito Santo. Bol. Mus. Biol. Mello Leitao, vol.11/12, p. 71-116.

BURBIDGE, AA., 1999. Conservation values and management of Australian islands for non-volant mammal conservation. Australian Conservation, vol. 21, no. 1, p. 67-74.

BUTLER, JRA., DU TOIT, JT. and BINGHAM, J., 2004. Free-ranging domestic dogs (Canis familiaris) as predators and prey in rural Zimbabwe: threats of competition and disease to large wild carnivores. Biol. Conserv., vol. 115, no. 3, p. 369-378.

CAVALCANTI, SM., 2003. Manejo e controle de danos causados por especies da fauna. In: CULLEN Jr., L., RUDRAN, R. and VALLADARES-PADUA, C. (Eds.). Metodos de Estudos em Biologia da Conservacao e Manejo da Vida Silvestre. Curitiba: Universidade do Parana.

CLEAVELAND, S., APPEL, MGJ., CHALMERS, WSK., CHILLINGWORTH, C., KAARE, M. and DYE, C., 2000. Serological and demographic evidence for domestic dogs as a source of canine distemper virus infection for Serengeti wildlife. Vet. Microbiol., vol. 72, no. 3-4, p. 217-227.

CONSERVATION INTERNATIONAL, 2000. Avaliacao e Acoes Prioritarias para a Conservacao da Biodiversidade da Mata Atlantica e Campos Sulinos. Brasilia: Conservation International.

COURTNAY, O., QUINNEL, RJ. and CHALMERS, WSK., 2001. Contact rates between wild and domestic canids: no evidence of parvovirus or canine distemper virus in crab- 19 eating foxes. Vet. Microbiol., vol. 81, no. 1, p. 9-19.

CUTLER, TL. and SWANN, DE., 1999. Using remote photography in wildlife ecology: a review. Wildl. Soc. Bull., vol. 27, no. 3, p. 571-581.

DANIELS, TJ. and BEKOFF, M., 1989. Population and social biology of free-ranging dogs, Canis familiaris. J. Mammal., vol. 70, no. 4, p. 754-762.

DEAN, W., 1995. With the Broadax and Firebrand, the Destruction of the Brazilian Atlantic Forest. Berkeley: University of California Press.

DEEM, SL. and EMMONS, LH., 2005. Exposure of free-ranging maned wolves (Chrysocyon brachyurus) to infectious and parasitic disease agents in the Noel Kempff Mercado National Park, Bolivia. J. Zoo. Wildl. Med., vol. 36, no. 2, p. 192-197.

FARREL, LE., ROMAN, J. and SUNQUIST, ME., 2000. Dietary separation of sympatric carnivores identified by molecular analysis of scats. Mol. Ecol., vol. 9, no. 10, p. 1583-1590.

FIELDING, WJ. and MATHER, J., 2001. Dog ownership in the west Indies: a case study from the Bahamas. Anthrozoos, vol. 14, no. 1, p. 72-80.

FIORELLO, CV., DEEM, SL., GOMPPER, ME. and DUBOVI, EJ., 2004. Seroprevalence of pathogens in domestic carnivores on the border of Madidi National Park, Bolivia. Anim. Conserv., vol. 7, no. 1, p. 45-54.

FIORELLO, CV., NOSS, AJ. and DEEM, SL., 2006. Demography, Hunting Ecology, and Pathogen Exposure of Domestic Dogs in the Isoso of Bolivia. Conserv. Biol., vol. 20, no. 3, p. 762-771.

FROLICH, K., CZUPALLA, O., HAAS, L., HENTSCHKE, J., DEDEK, J. and FICKEL, J., 2000. Epizootiological investigations of canine distemper virus in free-ranging carnivores from Germany. Vet. Microbiol., vol. 74, no. 4, p. 283-292.

FUNDACAO SOS MATA ATLANTICA and INSTITUTO DE PESQUISAS ESPACIAIS, 2004. Atlas dos Municipios da Mata Atlantica. <>. Cited Nov 2004.

GALETTI, M. and SAZIMA, I., 2006. Impacto de caes ferais em um fragmento urbano de Floresta Atlantica no sudeste do Brasil. Natureza e Conservacao, vol. 4, no. 1, p. 58-63.

GALINDO-LEAL, C. and CAMARA, I.G., 2003. Atlantic forest hotspot: An overview. In: GALINDO-LEAL, C. and CAMARA, IG. (Eds). The Atlantic Forest of South America. Biodiversity Status, Threats, and Outlook. Washington: Island Press. p. 3-11.

HAASS, L., HOFER, H., EAST, M., WOHLSEIN, P., LIESS, B. and BARRETT, T., 1996. Canine distemper virus infection in Serengeti spotted hyaenas. Vet. Microbiol., vol. 49, no. 1-2, p. 147-152.

HAMMER, AS., DIETZ, HH., ANDERSEN, TH., NIELSEN, L. and BLIXENKRONE-MOELLER, M., 2004. Distemper virus as a cause of central nervous disease and death in badgers (Meles meles) in Denmark. Vet. Rec., vol. 154, no. 17, p. 527-530.

HERRANZ, J., SUAREZ, F. and YANES, M., 2002. A low-cost photographic system to identify predators of ground-nesting bird nests. Game and Wildlife Science, vol. 19, no. 3, p. 179-195.

HOROWITZ, C., 1992. Plano de Manejo do Parque Nacional de Brasilia: Avaliacao da Metodologia de Planejamento adotada, Execucao e Resultados Alcancados no Decenio 79/89. Brasilia: Universidade de Brasilia. [Master Dissertation].

IBGE, 1993. Mapa de Vegetacao do Brasil. Fundacao Instituto Brasileiro de Geografia e Estatistica. Rio de Janeiro: IBGE.

-, 2003. Instituto Brasileiro de Geografia e Estatistica. <>. Cited Nov 2004.

KAYS, RW. and DEWAN, AA., 2004. Ecological impact of inside/outside house cats around a suburban nature preserve. Anim. Conserv., vol. 7, no. 3, p. 273-283.

KRUUK, H. and SNELL, H., 1981. Prey selection by feral dogs from a population of marine iguanas (Amblyhynchus cristatus). J. Appl. Ecol., vol. 18, no. 1, p. 197-204

LACERDA, ACR., 2002. Analise de ocorrencia de Canis familiaris no Parque Nacional de Brasilia: influencia da matriz, monitoramento e controle. Brasilia: Universidade de Brasilia. [Master Dissertation].

LAURANCE, WF., LOVEJOY, TE., VASCONCELOS, HL., BRUNA, EM., DIDHAM, RK., STOUFFER, PC., GASCON, C., BIERREGAARD, RO., LAURANCE, SG. and SAMPAIO, E., 2002. Ecosystem decay of Amazonian Forest fragments: a 22year investigation. Conserv. Biol., vol. 16, no. 3, p. 605-618.

LEPCZYK, CA., MERTIG, AG. and LIU, J., 2004. Landowners and cat predation across rural-to-urban landscapes. Biol. Conserv., vol. 115, no. 2, p. 191-201.

MANOR, R. and SALTZ, D., 2004. The impact of free-roaming dogs on gazelle kid/female ratio in a fragmented area. Biol. Conserv., vol. 119, no. 2, p. 231-236.

MARTINS, SS. and SANDERSON, JG., 2006. Monitoring mammals in the Caxiuana National Forest, Brazil--First results from the Tropical Ecology Assessment and Monitoring (TEAM) program. Biodiversity and Conservation. in press.

MCFADDEN, KW., WADE, SE., DUBOVI, EJ. and GOMPPER, ME., 2005. A Serological and Fecal Parasitologic Survey of the Critically Endangered Pygmy Raccoon (Procyon pygmaeus). J. Wildlife Dis., vol. 41, no. 3, p. 615-617.

MENDES, SL. and PADOVAN, MP., 2000. A Estacao Biologica de Santa Lucia, Santa Teresa, Espirito Santo. Bol. Mus. Biol. Mello Leitao, vol. 11/12, p. 7-34.

MURCIA, C., 1995. Edge effects in fragmented forests: implications for conservation. Trends Ecol. Evol., vol. 10, no. 2, p. 58-62.

MYERS, N., MITTERMEIER, RA., MITTERMEIER, CG., FONSECA, GAB. and KENT, J., 2000. Biodiversity hotspots for conservation priorities. Nature, vol. 403, no. 6772, p. 853-858.

ODELL, EA. and KNIGHT, RL., 2001. Songbird and medium-sized mammal communities associated with exurban development in Pitkin country, Colorado. Conserv. Biol., vol. 15, no. 4, p. 1143-1150.

OLIVEIRA, TG. and CAVALCANTI, SMC., 2002. Identificacao de Predadores de Animais Domesticos. In: PITMAN, MRPL., OLIVEIRA, TGR., PAULA, C. and INDRUSIAK, C. (Eds.). Manual de Identificacao, Prevencao e Controle de Predacao por Carnivoros. Brasilia: Instituto Brasileiro de Meio Ambiente e Recursos Naturais. p. 31-50.

PASSAMANI, M., MENDES, SL. and CHIARELLO, AG., 2000. Non-volant mammals of the Estacao Biologica de Santa Lucia and adjacent areas of Santa Teresa, Espirito Santo, Brazil. Bol. Mus. Biol. Mello Leitao, vol. 11/12, p. 201-214.

PIERPAOLI, M., BIRO, ZS., HERMANN, M., HUPE, K., FERNANDES, M., RAGNI, B., SZEMETHY, L. and RANDI, E., 2003. Genetic distinction of wildcat (Felis silvestris) populations in Europe, and hybridization with domestic cats in Hungary. Mol. Ecol., vol. 12, no. 10, p. 2585-2598.

RYAN, PR., ARANA, BA., RYAN, JR., WIRTZ, RA., WORTMANN, GW. and RIZZO, NR., 2003. The domestic dog, a potential reservoir for Leishmania in the Peten Region of Guatemala. Vet. Parasitol., vol. 115, no. 1, p. 1-7.

SECRETARIA MUNICIPAL DE SAUDE, 2003. Relatorio Anual da Secretaria Municipal de Saude de Santa Teresa/Setor de Vigilancia Ambiental em Saude--Ano 2002. Final Report. Unpublished Report. Santa Teresa: Secretaria Municipal de Saude.

-, 2004. Relatorio Anual da Secretaria Municipal de Saude de Santa Teresa/Setor de Vigilancia Ambiental em Saude--Ano 2003. Final Report. Unpublished Report. Santa Teresa: Secretaria Municipal de Saude.

SRBEK-ARAUJO, AC. and CHIARELLO, AG., 2005. Is camera-trapping an efficient method for surveying mammals in neotropical forests? A case study in south-eastern Brazil. J. Trop. Ecol., vol. 21, no. 1, p. 121-125.

THOMAZ, LD. and. MONTEIRO, R., 1997. Composicao floristica da Mata Atlantica de encosta da Estacao Biologica de Santa Lucia, municipio de Santa Teresa--ES. Bol. Mus. Biol. Mello Leitao, vol. 7, p. 3-48.

VILA, C. and WAYNE, RK., 1999. Hibridacion entre Perros y Lobos. Conserv. Biol., vol. 13, no. 1, p. 195-198.

WILSON, DE. and REEDER, DM., 2005. Mammal species of the World. A taxonomic and geographic reference. 3 ed. Washington: Johns Hopkins University Press.

Srbek-Araujo, AC. and Chiarello, AG. *

Programa de Pos-Graduacao em Zoologia de Vertebrados, Pontificia Universidade Catolica de Minas Gerais--PUC Minas, Av. Dom Jose Gaspar, 500, Bairro Coracao Eucaristico, CEP 30535-610, Belo Horizonte, MG, Brazil

* e-mail:
Table 1. Total number of type 1 records of mammals
obtained from February 2002 to February 2004 of camera
trapping in Santa Lucia Biological Station, Brazil. The
number of months with records and the average and range
of records/month are also shown. For comparative purposes,
species are arranged in decreasing number of records.
See Methods for details.

Species                                       Number    %

Dasyprocta leporina (Linnaeus, 1758)          44        15.07
Didelphis aurita Wied-Neuwied, 1826           44        15.07
Cuniculus paca (Linnaeus, 1766)               27        9.25
Canis lupus familiaris (Linnaeus, 1758)       25        8.56
Leopardus pardalis (Linnaeus, 1758)           24        8.22
Metachirus nudicaudatus (Desmarest, 1817)     15        5.14
Procyon cancrivorus (G. Cuvier, 1798)         15        5.14
Dasypus novemcinctus Linnaeus, 1758           14        4.79
Puma concolor (Linnaeus, 1771)                12        4.11
Mazama gouazoubira (G. Fischer, 1814) *       11        3.77
Nasua nasua (Linnaeus, 1766)                  11        3.77
Pecari tajacu (Linnaeus, 1758)                9         3.08
Rodentia unidentified                         8         2.74
Cabassous sp. **                              6         2.05
Cerdocyon thous (Linnaeus, 1766)              6         2.05
Sylvilagus brasiliensis (Linnaeus, 1758)      5         1.71
Sciurus aestuans Linnaeus, 1766               4         1.37
Eira barbara (Linnaeus, 1758)                 3         1.03
Leopardus tigrinus (Schreber, 1775)           2         0.68
Puma yagouaroundi (Lacepede, 1809)            2         0.68
Didelphimorphia unidentified                  2         0.68
Euphractus sexcinctus (Linnaeus, 1758)        1         0.34
Hydrochoerus hydrochaeris (Linnaeus, 1766)    1         0.34
Philander frenatus (Olfers, 1818)             1         0.34
Total                                         292       100

Species                                       Number    %

Dasyprocta leporina (Linnaeus, 1758)          19        76
Didelphis aurita Wied-Neuwied, 1826           15        60
Cuniculus paca (Linnaeus, 1766)               11        44
Canis lupus familiaris (Linnaeus, 1758)       12        48
Leopardus pardalis (Linnaeus, 1758)           15        60
Metachirus nudicaudatus (Desmarest, 1817)     12        48
Procyon cancrivorus (G. Cuvier, 1798)         8         32
Dasypus novemcinctus Linnaeus, 1758           8         32
Puma concolor (Linnaeus, 1771)                8         32
Mazama gouazoubira (G. Fischer, 1814) *       7         28
Nasua nasua (Linnaeus, 1766)                  8         32
Pecari tajacu (Linnaeus, 1758)                7         28
Rodentia unidentified                         6         24
Cabassous sp. **                              4         16
Cerdocyon thous (Linnaeus, 1766)              5         20
Sylvilagus brasiliensis (Linnaeus, 1758)      5         20
Sciurus aestuans Linnaeus, 1766               3         12
Eira barbara (Linnaeus, 1758)                 3         12
Leopardus tigrinus (Schreber, 1775)           2         8
Puma yagouaroundi (Lacepede, 1809)            2         8
Didelphimorphia unidentified                  2         8
Euphractus sexcinctus (Linnaeus, 1758)        1         4
Hydrochoerus hydrochaeris (Linnaeus, 1766)    1         4
Philander frenatus (Olfers, 1818)             1         4
Total                                         25        100

Species                                       Mean      Range

Dasyprocta leporina (Linnaeus, 1758)          1.76      0-8
Didelphis aurita Wied-Neuwied, 1826           1.76      0-11
Cuniculus paca (Linnaeus, 1766)               1.08      0-6
Canis lupus familiaris (Linnaeus, 1758)       1         0-8
Leopardus pardalis (Linnaeus, 1758)           0.96      0-4
Metachirus nudicaudatus (Desmarest, 1817)     0.6       0-2
Procyon cancrivorus (G. Cuvier, 1798)         0.6       0-4
Dasypus novemcinctus Linnaeus, 1758           0.56      0-4
Puma concolor (Linnaeus, 1771)                0.48      0-3
Mazama gouazoubira (G. Fischer, 1814) *       0.44      0-3
Nasua nasua (Linnaeus, 1766)                  0.44      0-2
Pecari tajacu (Linnaeus, 1758)                0.36      0-2
Rodentia unidentified                         0.32      0-2
Cabassous sp. **                              0.24      0-2
Cerdocyon thous (Linnaeus, 1766)              0.24      0-2
Sylvilagus brasiliensis (Linnaeus, 1758)      0.2       0-1
Sciurus aestuans Linnaeus, 1766               0.16      0-2
Eira barbara (Linnaeus, 1758)                 0.12      0-1
Leopardus tigrinus (Schreber, 1775)           0.08      0-1
Puma yagouaroundi (Lacepede, 1809)            0.08      0-1
Didelphimorphia unidentified                  0.08      0-1
Euphractus sexcinctus (Linnaeus, 1758)        0.04      0-1
Hydrochoerus hydrochaeris (Linnaeus, 1766)    0.04      0-1
Philander frenatus (Olfers, 1818)             0.04      0-1
Total                                         11.7      0-11

* In a previous study (Srbek-Araujo and Chiarello, 2005) this
deer species was identified as M. americana. Further
comparisons carried out after publication indicated, however,
that the correct pictured species is M. gouazoubira.

** Cabassous tatouay have been collected in the region
of Santa Teresa, but the poor quality of pictures
obtained in the present study does not guarantee an
unequivocal identification.
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Author:Srbek-Araujo, A.C.; Chiarello, A.G.
Publication:Brazilian Journal of Biology
Date:Nov 1, 2008
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