INTRODUCTION
Commercial fisheries occur worldwide, affecting target and non-target species, with important impacts on marine ecosystems (Alverson et al., Reference Alverson, Freeberg, Pope and Murawski1994; Gislason et al., Reference Gislason, Sinclair, Sainsbury and O'Boyle2000). Sea turtles are caught as bycatch (incidental capture of non-target species) in several fisheries. When captured, they are often thrown back into the sea, most of the time injured, drowning or dead (Oravetz, Reference Oravetz, Eckert, Bjorndal, Abreu-Grobois and Donnelly2000). The impact of bycatches of non-target populations depends on the life history of the impacted species (Alverson et al., Reference Alverson, Freeberg, Pope and Murawski1994). Due to their long lifespan and late maturation (long juvenile period), sea turtle populations, both adult (reproductive) and juvenile individuals, are highly vulnerable to mortality (Crouse et al., Reference Crouse, Crowder and Caswell1987).
All sea turtle species are protected by the Convention on International Trade in Endangered Species of Wild Fauna and Flora (CITES, 2015) and listed as threatened or endangered in the International Union for the Conservation of Nature's Red List (IUCN, 2015). Nevertheless, commercial fisheries continue to threaten sea turtle species due to incidental fishing mortality. Thus, top research and conservation priorities include the identification of areas where sea turtles and fisheries overlap, quantification of the impacts on sea turtle populations and the development of solutions to either reduce capture or increase turtle post-capture survival without causing economic losses to fishery activities (National Research Council, 1990; Domingo et al., Reference Domingo, Bugoni, Prosdocimi, Miller, Laporta, Monteiro, Estrades and Albareda2006; FAO, 2009). Since the 1970s, studies evaluating the mortality of sea turtles in trawl fisheries in South Atlantic and Gulf of Mexico have been conducted, and some estimates indicate that more than 10,000 turtles die from bycatch per year (Roithmayr & Henwood, Reference Roithmayr and Henwood1982; Henwood & Stuntz, Reference Henwood and Stuntz1987; National Research Council, 1990). These estimates provided the basis for the development of the Turtle Excluder Device (TED), an inclined metal grid placed in the trawl to prevent large animals from entering the cod-end. A small opening in the trawl is located either above or below the grid, which allows specimens stopped by the TED to escape, relatively unharmed. Targeted species such as shrimp, however, flow to the back of the cod-end (FAO, 2009).
The size of the continental shelf and habitat variability across several degrees of latitude provide shelter for a high diversity of marine fauna within the Tropical South-western Atlantic (Briggs, Reference Briggs1995). Currently, Brazil is ranked as the 23rd wild marine fish producer (extractive fishing) in the world, contributing to about 7% of the national Gross Domestic Product (GDP). With 90,559 tons produced in 2010, the south-eastern region of Brazil is ranked third in wild marine fish production within the country (MPA, 2012). Commercial bottom trawl fishery in south-east Brazil targets shrimps, crabs and an array of bottom-dwelling and demersal fish species. Due to the overcapacity of the fishing fleet, stocks are considered to be overexploited since 2002 (Domingo et al., Reference Domingo, Bugoni, Prosdocimi, Miller, Laporta, Monteiro, Estrades and Albareda2006; Perez & Pezzutto, Reference Perez and Pezzuto2006). Currently, there are ~1500 industrial trawlers working off the south-eastern Brazilian coast (MPA, 2012).
Five species of sea turtles occur in Brazil: loggerhead (Caretta caretta), leatherback (Dermochelys coriacea), olive ridley (Lepidochelys olivacea), green (Chelonia mydas) and hawksbill (Eretmochelys imbricata) turtles (Peres et al., Reference Peres, Magris and Ribeiro2011). Monitoring and reducing bycatch and increasing awareness of the problem in the political arena are three of the main goals of the National Plan for the Conservation of Sea Turtles in Brazil (ICMBio, Reference Marcovaldi and Santos2011). Catch per unit efforts (CPUE) of sea turtle bycatch by pelagic longline fisheries have been estimated for the loggerhead turtle (CPUE = 0.8712/1000 hooks) and the leatherback turtle (CPUE = 0.1527/1000 hooks) (Sales et al., Reference Sales, Giffoni and Barata2008). Corresponding CPUE of sea turtles for bottom trawl fishery in Brazil, however, have been unavailable until now. The bycatch of sea turtles in the Brazilian trawl fishery has been previously inferred based on stranding data (Marcovaldi et al., Reference Marcovaldi, Sales, Thomé, Silva, Gallo, Lima, Lima and Bellini2006; Reis et al., Reference Reis, Silveira and Siciliano2009; Silva et al., Reference Silva, Castilhos, Santos, Brondízio and Bugoni2010). In this context, the present study provides estimates of CPUE sea turtle bycatches by the industrial bottom trawl fishery in the Tropical Southwestern Atlantic area of Brazil, aiming to (1) verify the distribution of the operational area of vessels participating in the study; (2) identify which sea turtles species interact with this fishery; (3) verify which abiotic variables (depth, period of the day, geographic coordinates) may influence sea turtle capture; and (4) compare the CPUE estimates presented herein with others calculated worldwide.
MATERIALS AND METHODS
Study area
South-eastern Brazil has 1890 km of coastline throughout the states of Espírito Santo (ES), Rio de Janeiro (RJ) and São Paulo (SP). These areas are characterized by the tropical humid climate of the Tropical South-western Atlantic (Neto, Reference Neto2005; IBGE, 2012). The width of the south-eastern continental shelf varies between 50 and 230 km (Ruffato, Reference Ruffato2011). Water masses in the region include the Tropical Water mass (high temperature and salinity), the South Atlantic Central Water mass (low temperature and relatively low salinity) and the Coastal Water mass (high temperature and low salinity) (Martins et al., Reference Martins, Olavo, Costa, Costa, Martins and Olavo2005).
The vessels monitored in this survey belong to Brazil's south-eastern industrial bottom trawl fleet, which lands its catch in the port city of Niterói (inside the Guanabara Bay), in Rio de Janeiro (22°52′S 43°6′W).
Data collection
A voluntary logbook programme was implemented between July 2010 and December 2011 to monitor sea turtle bycatch in the trawl fisheries. The captains of three shrimp and one fish trawler collected the data. The fleet owner allowed captains to participate in the data collection for this study. Data were not collected from 1 March to 31 May, due to the annual closure of the fishery (Instrução Normativa IBAMA no 189 de, 2008).
The vessels were about 22 m in overall length (LOA) and operated two otter trawls coupled with two pairs of wooden doors measuring ~2.3 m in length and 90 cm in height. Head-rope length was consistent between all boats, measuring 28.0 m. Trawling speed ranged from 2.0 to 2.6 nm h−1. Fishing trips lasted between 10 to 15 days, and vessels typically executed two trips per month. For each trip, between 60–70 tows each lasting 4.2 ± 0.9 h were performed.
All vessel captains recorded the date, time, bottom depth and GPS location (deploying and hauling of trawls) for all tows in both the project and the official logbooks (MMA, 2005). Captains were trained to collect information related to turtle bycatches, namely: turtle species, curved carapace length (CCL) and width (CCW) (Bolten, Reference Bolten, Eckert, Bjorndal, Abreu-Grobois and Donnelly2000), and whether the turtle was alive (lively movements), dead/comatose (no breathing, eyes not responding to touch) or drowned (no lively movements but eyes responding to touch). To identify species, the captains used a simplified sea turtle identification key provided with the data collection sheets. To confirm the identified species, the captains photographed the bycaught turtles and project personnel validated this upon return to the docks.
To identify fishing zones of the monitored vessels trawl deployment, GPS coordinates of all recorded tows were plotted. Hauling GPS coordinates were used to plot sea turtle captures, since the capture is only verified when the trawl is hauled back on the boat. Maps were generated using the software Quantum Gis 2.14 package.
Data analysis
Generalized Linear Models (GLMs) were used to detect which variables influence turtle bycatch by the trawlers monitored in this study (Vernables & Dichmont, Reference Vernables and Dichmont2004). The number of turtles captured in each tow was included as a response variable under the influence of the following fixed variables: (1) fishing time (hour) at the beginning of each tow (in decimals); (2) water depth (in metres), taken at the end of each tow; (3) tow duration – time (hours) elapsed between the deployment and hauling of each tow; (4) latitude; and (5) longitude taken in decimal degrees at the beginning of each tow.
Models were constructed step-by-step by reducing the full model, which initially included all the fixed variables (Tavares et al., Reference Tavares, Guadagnin, Moura, Siciliano and Merico2015), using the binomial family as the best error distribution, followed by graphical diagnostics (Crawley, Reference Crawley2007; Zuur et al., Reference Zuur, Ieno, Walker, Saveliev and Smith2009). The models were selected according to Akaike's Information Criterion (AIC), where the best models produce the lowest AIC scores (Burnham & Anderson, Reference Burnham and Anderson2002). As small differences in AIC scores indicate equally supported models, model averaging was performed via the zero method, using a cut-off of 2 AIC (Grueber et al., Reference Grueber, Nakagawa, Laws and Jamison2011; Tavares et al., Reference Tavares, Guadagnin, Moura, Siciliano and Merico2015). The importance value for each predictive variable was also calculated as the sum of the Akaike weights along a chain of randomly generated models starting from the full model (Burnham & Anderson, Reference Burnham and Anderson2002).
The statistical analyses were performed with the software R 3.0.1, using the following packages: ‘stats’ for model fit, ‘MuMIn’ for model averaging and estimating the importance of variables and ‘bbmle’ for calculating the AIC values (R Core Team, 2013). In addition, the modelling procedures were preceded by a data exploration step, in which outliers, collinearity, and other possible problems were verified, as pointed out by Zuur et al. (Reference Zuur, Ieno and Elphick2010). Model assumptions were checked by the graphical inspection of the residues. The analysis of collinearity between variables did not exceed a Variance Inflation Factor (VIF) of 2, except for longitude (VIF = 5.83) and latitude (VIF = 7.92).
The catch per unit efforts (CPUE) were calculated using fishing hours as the sample unit. The total number of captured turtles was divided by the total number of fishing hours and multiplied by 1000 (turtles per 1000 h of towing). To compare the calculated estimates with the available literature from the Gulf of Mexico and south-eastern North Atlantic (Henwood & Stuntz, Reference Henwood and Stuntz1987), prawn fishery of Northern Australia (Poiner & Harris, Reference Poiner and Harris1996), north-eastern Venezuela (Alió et al., Reference Alió, Marcano and Altuve2010), Queensland, Australia (Robins, Reference Robins1995) and the Pacific side of Costa Rica (Arauz et al., Reference Arauz, Vargas, Naranjo, Gamboa and Witzell1997), the efforts per towing hours were based on a single trawl with 30.5 m head-rope length. All the compared studies used the same standardization method, using the formula according to Henwood & Stuntz (Reference Henwood and Stuntz1987):
$$Ei = nt(H/30.5\,{\rm m})$$Where n = number of nets; t = trawling time (h); and H = head-rope length (m).
Turtle CPUE and confidence intervals (95% CI) were calculated according to Snedecor & Cochran (Reference Snedecor and Cochran1967) using the formula:
$$\mathop {R} \limits^{\frown} = \sum\limits_{i = 1}^n {Ti/\sum\limits_{i = 1}^n {Ei}} $$where 
$\mathop {R} \limits ^{\frown} $ = CPUE; Ti = number of turtles captured; Ei = effort (30.5 m net hour); and n = sample size (number of tows).
Confidence intervals (95% CI) were calculated using the formulas below:
$${\rm CI} = \mathop {R} \limits ^{\frown} + 1.96\,s\mathop{R} \limits ^{\frown}, \;{\rm and\!\!:} $$
$$s(\mathop {R} \limits ^{\frown}) = (1/\bar E)\sqrt {\displaystyle{{\sum\nolimits_{i = 1}^n {(Ti - \mathop {R} \limits ^{\frown} Ei)^2}} \over {n(n - 1)}}} $$Where 
$\mathop {R} \limits ^{\frown}$ = estimated average CPUE (turtles/single 30.5 m trawl per hour); 
$s(\mathop {R} \limits ^{\frown})$ = estimated CPUE; and 
$\bar E$ = the average size of the unit effort in the sample (average tow duration = 4.2 h).
RESULTS
A total of 1996 hauls were recorded during 353 fishing days, totalling 8313 trawling hours. Trawling efforts were distributed between 25°S 46°W and 21°S 40°W, but mostly concentrated off the coast of Rio de Janeiro, due to the proximity of the port to the fishing grounds (Figure 1). Tow duration ranged between 20 and 535 min (mean = 251, SD = 55) and tow depths ranged between 24 and 130 m, with most hauls at ~60 m (mean = 59, SD = 22). Fishing efforts were slightly higher during the day (4338 h) when compared with night-time (3975 h).
Geographic distribution of hauls reported during the survey along the states of São Paulo, Rio de Janeiro and Espírito Santo. The inset shows South America, Brazil and the Brazilian south-eastern region. GB, Guanabara Bay.
A total of 44 sea turtles were bycaught by the monitored vessels, resulting in a CPUE ± 95% CI of 5.3 ± 0.8 turtles per 1000 h. Fishing efforts were concentrated off the coast of the state of Rio de Janeiro (Figure 2). The captured species were loggerhead (N = 22), olive ridley (N = 21), and green (N = 1) turtles. No mortality was documented, but one drowned turtle was recorded. The curved carapace length (CCC) ranged between 61 and 150 cm (mean = 83.5, SD = 22.3) for loggerheads, 56 and 76 cm (mean = 64.3, SD = 4.8) for olive ridleys, and the single green turtle individual measured 38.5 cm. Most sea turtle catches (N = 34) occurred within the 60 m isobath, which concentrated 63.4% of the total fishing efforts (N = 5272 h).
Geographic and depth distribution of sea turtle catches, by species, off the south-eastern Brazilian coast. GB, Guanabara Bay.
Five GLMs fitted with binomial errors showed similar performance in predicting sea turtle bycatches (ΔAIC < 2) (Table 1). The small differences in AIC scores prevented the choice of a single best fitting model. According to the model-averaged parameter estimates, sea turtle bycatch by trawl fishery is affected mainly by water depth (Table 2). The model-averaged coefficient indicated that the probability of sea turtle bycatch increases slightly with reduced trawling depth.
Ranking of the best fitted Binomial Generalized Linear Models for sea turtle incidental captures by the trawl fishery as function of predictive variables off the coast of Rio de Janeiro, Brazil.
ΔAIC, Akaike's information criterion; w i, Akaike weights.
Statistics for the Binomial Generalized Linear Model for sea turtle incidental captures by the trawl fishery as functions of predictive variables off the coast of Rio de Janeiro, Brazil. Water depth was the only significant variable (*).
CI, confidence interval; Z, Wald Z test output; P, statistical significance.
To compare the present results with other studies on sea turtle bycatch by trawl fisheries, a standardized effort (Ei) of 15,263 towing hours was obtained, with a CPUE ± 95% CI of 0.0029 ± 0.004 turtles per towing hour (Table 3).
Standardized CPUE (turtles per towing hour) obtained in this study compared with other sea turtle catches in trawl fisheries studies conducted worldwide. Data are presented from highest to lowest CPUE.
EI, Eretmochelys imbricata; CM, Chelonia mydas; CC, Caretta caretta; LO, Lepidochelys olivacea; DC, Dermochelys coriacea; LK, Lepidochelys kempii; ND, Natator depressus.
DISCUSSION
Captured species and influential factors
The species most captured by bottom trawlers in south-eastern Brazil were adult and sub-adult loggerhead and olive ridley turtles. This pattern has been reported in several studies around the world. The loggerhead turtle is the species most affected by bottom trawls (Table 3) (Poiner & Harris, Reference Poiner and Harris1996; Casale et al., Reference Casale, Laurent and De Metrio2004; Kuhnert et al., Reference Kuhnert, Griffihs and Brewer2011; Domènech et al., Reference Domènech, Bitón, Merchán, Revuelta, Vélez-Rubio, Tomás and Belskis2013), with high catches apparently associated to local species abundance and favourable environmental conditions, such as warm waters and food availability (Robins, Reference Robins1995; Casale et al., Reference Casale, Laurent and De Metrio2004). The loggerhead turtle is the most abundant nester of all five species in Brazil (Marcovaldi & Chaloupka, Reference Marcovaldi and Chaloupka2007) with important nesting areas in northern Rio de Janeiro and Espírito Santo (Marcovaldi & Marcovaldi, Reference Marcovaldi and Marcovaldi1999; Lima et al., Reference Lima, Wanderline, Almeida, Lopez and Goldberg2012), which may explain the high bycatch rates of adult individuals in bottom trawl fishery.
High capture rates of olive ridleys have been associated with local abundance and proximity to nesting sites (Casale et al., Reference Casale, Cattarino, Freggi, Rocco and Argano2007; Murray, Reference Murray2008). Sales et al. (Reference Sales, Giffoni and Barata2008) recorded the capture of 71 olive ridleys in longlines between latitudes 10°N and 10°S, where nesting occurs. However, nesting sites for this species in Brazil are located in the north-eastern region, far from the present study area. Thus, captures between 35°S and 15°S are not linked to nesting behaviour, but rather with feeding behaviour. Studies based on carcasses found washed ashore and telemetry of live individuals in south-eastern Brazil show that olive ridleys nesting in north-east Brazil move southward to Rio de Janeiro in order to feed. Feeding and resting areas for this species seem to overlap with the area fished by trawlers. Furthermore, this region may be an important foraging ground for olive ridleys (Lemke et al., Reference Lemke, Frazier, Thomé, Almeida, Juarez and Pilcher2003; Reis et al., Reference Reis, Silveira and Siciliano2009) and the results presented herein provide additional evidence to support this hypothesis.
Water depth was the most significant variable associated with sea turtle bycatch. Sea turtles show a wide range in diving depth and duration, but most species spend more time in shallow waters (Lutcavage & Lutz, Reference Lutcavage, Lutz, Lutz and Musick1996). Olive ridleys usually perform longer and deeper dives than loggerheads, but both species spend most of their time in waters less than 60 m in depth (Polovina et al., Reference Polovina, Howell and Balaz2003; Swimmer et al., Reference Swimmer, Arauz, McCracken, Naughton, Ballestero, Musyl, Bigelow and Brill2006). Diving depth is also associated with water temperature and activity level. Deeper dives usually occur during resting periods in cold waters, with reduced activity (Hochscheid et al., Reference Hochscheid, McMahon, Bradshaw, Maffucci, Bentivegna and Hays2007; Murray, Reference Murray2008). The warm surface Tropical Water mass (TW) and the cold sub-surface South Atlantic Central Water mass (SACW) are the most important water masses influencing the continental shelf in south-eastern Brazil. During the spring-summer, prevailing north-easterly winds generate a coastal upwelling of the SACW, centred at 42°W, where the continental shelf is narrow, providing an important sea turtle feeding ground which may lead to bycatches during foraging or resting periods (Polovina et al., Reference Polovina, Balazs, Howell, Parker, Seki and Dutton2004; Amorocho & Reina, Reference Amorocho and Reina2007).
Impact of trawl fisheries on sea turtles
The present study indicated that the CPUE calculated in this study was the sixth highest when compared with similar studies conducted worldwide. The fact that the estimates herein are within the range recorded by other researchers who used on-board observers (Henwood & Stuntz, Reference Henwood and Stuntz1987; Arauz et al., Reference Arauz, Vargas, Naranjo, Gamboa and Witzell1997; Alió et al., Reference Alió, Marcano and Altuve2010) suggests that voluntary data collection by boat captains may be an efficient way of providing estimates of sea turtle catches and CPUE.
Four of six studies used for comparative analyses indicate that loggerhead and olive ridley turtles are the main bycaught species. Differences in CPUE between the species may be due to the differences in the distribution and population size of bycaught species. For instance, the flatback turtle (Natator depressus), endemic to Australian waters, is the most common sea turtle species bycaught in bottom trawls in that area, with loggerheads being the second most bycaught species (Poiner & Harris, Reference Poiner and Harris1996). Green turtles are often captured in shallow coastal waters (Robins, Reference Robins1995; Arauz et al., Reference Arauz, Vargas, Naranjo, Gamboa and Witzell1997; Alió et al., Reference Alió, Marcano and Altuve2010) where this species is commonly found (Marquez, Reference Marquez1990).
The present study demonstrated that trained vessel captains from industrial trawlers operating in the Tropical South-western Atlantic could provide data on sea turtle bycatches. Trust was built between the research team and collaborative captains in order to obtain reliable estimates. However, underreporting could still have occurred, resulting in underestimates of sea turtle CPUEs, as captains may have been reticent to report catches due to possible penalties foreseen in the Brazilian legislation. Despite the criticism of using logbook information data (FAO, 2009), this information may be relevant when better information is lacking (Robins, Reference Robins1995; Poiner & Harris, Reference Poiner and Harris1996). Developing collaborative fisheries research is essential to obtain reliable data, to evaluate the demographic effects of bycatches and to achieve progress in bycatch mitigation (Soykan et al., Reference Soykan, Moore, Zydelis, Crowder, Safina and Lewison2008; Sales et al., Reference Sales, Giffoni, Fiedler, Azevedo, Kotas, Swimmer and Bugoni2010). Thus, this initiative may be a good starting point leading to additional research programmes, especially since research funds are limited.
Using TEDs is currently mandatory in Brazil, but the industry often neglects their use in trawls, since boat captains claim that TEDs reduce the catch volume of target species. To date, no complete comparison experiments have been conducted to determine TED efficiency in Brazilian waters. In addition, captains indicate that little information, instructions or training activities on proper TED use are available, which inhibits the use of this equipment by crews (Tamar-Ibama, 2007). Since TED use is currently not widespread, it could be worthwhile to teach captains best handling practices for turtles when captured, such as learning turtle reanimation techniques which could aid in reducing turtle mortality in this fishery (FAO, 2009). The information presented herein indicates that the bycatch of sea turtles by the bottom trawl fisheries within the Brazilian Exclusive Economic Zone (EEZ) waters in the Tropical South-western Atlantic occurs at levels that may affect sea turtle conservation efforts. Systematic monitoring of bottom trawl fisheries is, thus, required to further understand bycatch levels and to provide additional data for improved evaluations of sea turtle populations, which will in turn benefit the conservation of these animals.
ACKNOWLEDGEMENTS
We thank all boat captains and the owner of the company for their voluntary participation in this study. Without the captains’ goodwill, this study would not have been possible.
FINANCIAL SUPPORT
S.M.G. and C.M.N. held fellowships from Conselho Nacional de Desenvolvimento Científico e Tecnológico – CNPq during this study. D.C.T. is supported by Coordenação de Aperfeiçoamento de Pessoal de Nível Superior-CAPES.
