Line transect estimates of Irrawaddy dolphin abundance along the eastern Gulf Coast of Thailand

Introduction

As coastal areas are increasingly impacted by human population growth and development, gaps in knowledge about the abundance and habitat extents of coastal marine mammals obstruct effective management and conservation (Dawson et al., 2008; Dick and Hines, 2011). In many developing coastal regions, the extent and severity of threats (i.e., bycatch, pollution, overfishing) is largely unknown, and cannot be quantitatively evaluated without high quality abundance data (Dawson et al., 2008). Repeatable and practical methods have been outlined (Dawson et al., 2008) and tested (see for example Kreb, 2004; Hines et al., 2005; Dick and Hines, 2011; Minton et al., 2013) in remote areas and developing countries for line transect distance sampling surveys (Buckland et al., 2001). As part of a long-term research project to assess marine mammal abundance, distribution and threats along the eastern Gulf coast of Thailand, primarily in Trat Province, we found a relatively large population of Irrawaddy dolphins (Orcaella brevirostris) and have had repeated sightings of two other species:Indo-Pacific humpback dolphins (Sousa chinensis) and Indo-Pacific finless porpoises (Neophocaena phocaenoides). None of these species had been studied in this area previous to our project's commencement in 2008. However, the numbers of sightings of humpback dolphins and finless porpoises were not large enough to permit a distance sampling analysis. In this paper we report on the results of our line transect surveys for Irrawaddy dolphins for 5 years: 2008, 2009, 2012, 2013, and 2014.

Irrawaddy dolphins can be found in riverine, estuarine and coastal waters throughout the tropical and subtropical Indo-Pacific region (Stacey and Arnold, 1999; Minton et al., 2013). Throughout Southeast Asia, the Irrawaddy dolphin is generally found in shallow estuaries and coastal waters (Reeves et al., 2008). For example, in the Philippines, most sightings were made at a depth of < 6 m (Dolar et al., 2002). Largely because they are distributed close to coastal areas, Irrawaddy dolphins are exposed to coastal development and fishing activities likely to result in them becoming incidental bycatch (Dolar et al., 2002; Reeves et al., 2003). Little is known about nearshore Irrawaddy dolphins in the Gulf of Thailand. Chantrapornsyl et al. (1996), Stacey and Leatherwood (1997); Stacey and Arnold (1999), and Anderson and Kinze (1999) note that while records of occurrence are few, Irrawaddy dolphins have been reported along the coast of the Gulf of Thailand, with an early report of a skull found in Khlong Yai, in Trat province, in 1914 (Anderson and Kinze, 1999). The International Union for the Conservation of Nature (IUCN) classes the Irrawaddy dolphin as a vulnerable species with a decreasing trend on its Red List of Threatened Species (Reeves et al., 2008). In Thailand, the Irrawaddy dolphin is included under the 1992 Wild Animals Preservation and Protection Act. In the IUCN/SSC Cetacean Specialist Groups' 2002–2010 Conservation Action Plan for the World's Cetaceans, one of the recommended research initiatives concerning the status of coastal cetaceans in Thailand addresses a need to identify areas of “cetacean abundance for special conservation attention,” as well as to document fishing intensity in these areas (Reeves et al., 2003, p. 60). These dolphins are a species of concern in Thailand, as evidenced by Thailand's sponsorship of Irrawaddy dolphins for CITES Appendix I protection in Bangkok at the Conference of the Parties in 2004 (CITES, 2004).

Within Thailand, Irrawaddy dolphins are distributed in Phang Nga and Krabi Bays as well as Satun Province along the Andaman Sea coast, Songkhla Lake, and several locations around the Gulf of Thailand (Bonhote, 1904; Pilleri and Gihr, 1974; Chantrapornsyl et al., 1996; Stacey, 1996; Adulyanukosol, 1999; Anderson and Kinze, 1999; Chantrapornsyl et al., 1999; Beasley et al., 2002; Smith et al., 2003; Perrin et al., 2005; Kittiwattanawong et al., 2007; Reeves et al., 2008) (Figure 1). The species has additionally been reported to occur within the Chao Phraya and Bang Prakong rivers (Adulyanukosol, 1999). Little is known about Irrawaddy dolphins along the Andaman Sea coast of Thailand. Occurrence records for Phang Nga and Krabi Bays are limited to fishermen's reports (Chantrapornsyl et al., 1996), while this species has been sighted off the Satun coast around Tarutao Island (Adulyanukosol, 1999; Perrin et al., 2005). The subpopulation in Songkhla Lake is considered Critically Endangered by the IUCN (Reeves et al., 2008). It is currently thought that Irrawaddy dolphins in the Lake number fewer than 30 individuals (Jutapruet, 2013), and are threatened by direct capture for Oceanaria, entanglement in fishing gear, habitat degradation, pollution, prey depletion due to overfishing, and inbreeding depression due to small population size and demographic isolation (Stacey, 1996; Beasley et al., 2002; Perrin et al., 2005; Kittiwattanawong et al., 2007; Reeves et al., 2008; Jutapruet, 2013).

FIGURE 1

Figure 1. Map of Thailand with Irrawaddy dolphin sighting areas mentioned in the text.

Irrawaddy dolphins occur in many locations along the coast surrounding the Gulf of Thailand, from Surat Thani and Pattani Provinces on the western Gulf coast, through Samut Songkhram, Samut Sakhon, and Samut Prakan Provinces in the northern Gulf, to Chonburi, Rayong, Chanthaburi, and Trat Provinces on the eastern Gulf coast (Chantrapornsyl et al., 1996, 1999; Adulyanukosol, 1999; Anderson and Kinze, 1999). Generally, threats to Irrawaddy dolphins around the Gulf of Thailand include entanglement in fishing gear; habitat degradation due to coastal zone development, tourism, agriculture, aquaculture, and manufacturing; pollution from waste runoff; and live capture for Oceanaria (Perrin et al., 2005). In August of 1994, two Irrawaddy dolphins were found stranded in Surat Thani Province and one more stranded between 1996 and 1999 (Chantrapornsyl et al., 1996; Adulyanukosol, 1999). One stranding was recorded in Samut Songkhram Province (Adulyanukosol, 1999). In Trat Province, where this research took place, bycatch seems to be the most critical threat to Irrawaddy dolphins. Between 2010 and 2012, fishermen reported accidentally catching and killing 21 Irrawaddy dolphins, 10 of which were entangled in gillnets (Whitty, 2014). Over a period of 14 days in January and February 2013, 14 Irrawaddy dolphins and 3 finless porpoises were discovered stranded or dead in illegal fishing gear along the Trat coast. Necropsies confirmed that 10 of the animals were incidentally entangled in illegal fishing gear, although one of the finless porpoises had died due to parasites. For six, the cause of death was not determined due to decomposition (Junchompoo et al., 2014).

The goal of this research was to assess the conservation status of coastal cetaceans in Trat province. Information about the abundance of these dolphins is necessary to gauge the effects of bycatch, habitat degradation and other threats on the sustainability of this population. This assessment is urgently needed to contribute effectively to local/regional conservation and possible protected area management schemes, especially in a rapidly developing area.

Materials and Methods

Trat Province is at the eastern boundary of Thailand, approximately 315 km east of Bangkok, extending to the Cambodian border (Figure 1). The northern coast of the Province is adjacent to an archipelago of islands. The northernmost island, Ko Chang, is a popular tourist area. Further east, into our field site, is Trat Bay, a wide, shallow bay with two large rivers emptying into it. The eastern extent of the Province is a narrow strip, at one point 1.5 km wide and 45 km long, with the steep Cardamom Mountains in Cambodia forming a natural border. Besides the city of Trat, above Trat Bay, Khlong Yai, a major fishing port, and Hat Yai, at the Cambodian border, the coast is relatively sparsely populated with fishing villages. The climate is tropical, with a dry season between November and March, and a wet southwest monsoon from April through November. According to tidal charts from the Royal Thai Navy, the tidal range is at maximum 3.0 m.

For analysis of patterns of distribution and habitat use in further research, we divided our survey area into three strata, based on variations of geography and human use. The north stratum was in eastern Trat Bay, the middle, further down the strip, near the entrances of several rivers into coastal waters, and the south stratum near the fishing port of Khlong Yai toward the Cambodian border. During the surveys, our boat moved along zig-zag transect lines in each of the three survey strata: north, middle, and south (see Figure 2).

FIGURE 2

Figure 2. (A) All on-effort sightings of Orcaella brevirostris in 2008 and 2009 surveys along the coast of Trat Province, on the eastern Gulf coast of Thailand. The purple area is the north strata closer to the shallow Bay. The green area is the shallow middle strata near several river mouths. The orange area is the south strata, a deeper area closer to the major fishing port of Khlong Yai. (B) All on-effort sightings of Orcaella brevirostris in 2012 and 2013 surveys along the coast of Trat Province, on the eastern Gulf coast of Thailand. (C) All on-effort sightings of Orcaella brevirostris in 2014 surveys along the coast of Trat Province, on the eastern Gulf coast of Thailand.

Distance sampling surveys along line transects are widely used to estimate density and abundance of cetacean populations (Buckland et al., 2001). We used Distance software (Thomas et al., 2010) and a geographic information system to design a line transect survey design for Irrawaddy dolphins in a stratified study area in the eastern Gulf coast of Thailand during five field seasons in 2008, 2009, 2012, 2013, and 2014. Our zig-zag survey design for boat-based transects is based on Strindberg and Buckland (2004). The design ensured reasonably even sampling probabilities across the study area (even sampling probabilities are an assumption underlying a standard distance sampling analysis), while maximizing on-effort time, or time spent following the transect looking for animals. Field ground-truthing of each line was conducted to account or adjust for shallow or impassable areas and to ensure the transect lines could be run in perpetuity with minimal difficulty. Our goal was to design a practical and repeatable systematic survey for this area that would allow for quantitative analysis of abundance and long-term monitoring of the dolphins in this area.

Surveys were conducted in January or February of each year, during the north-east monsoon, which has a lower change of rainfall in the eastern Gulf. Each year, the number of transect days varied, according to weather. Transects were completed in all strata in the survey area either two (2012, 2013, 2014) or three times (2008, 2009) in a field season. All surveys were run from a 12-m fishing boat equipped with inboard engines, boat speed was kept at 10 kmh⁻¹. A team of three observers continuously scanned from the bow to 90° Port and Starboard with the naked eye and 7 × 50 binoculars while on effort. For each dolphin group sighting detected during on-effort searching, waypoints were recorded into a handheld GPS unit at the sighting location, then three variables necessary to estimate density and abundance were immediately recorded: the estimated radial distance from the survey boat (r) using binoculars with reticles, the angle (θ) between the transect line and the line of the detection using angle boards, and the number of animals seen. Once the initial data were recorded, the boat deviated from the transect to approach the dolphin group off effort, to within 10 m to record their location using the GPS unit. We also collected data on the species and number of animals in the group, general age composition (adult or calf), photographs for photo-identification when possible, behavioral data and environmental parameters. Afterwards, we returned to the location where the sighting was made and resumed transect effort. Environmental parameters were collected for each sighting, as well as every 30 min while on transect.

Density of Irrawaddy dolphin groups within the area surveyed is estimated as ${\widehat{D}}_s=\frac{n\widehat{f}(0)}{2L}$, where L denotes the aggregate length of the transects, n is the number of groups observed, f(0) is the probability density function of observed perpendicular distances evaluated at zero distance from the line. The density of groups ${\widehat{D}}_s$ is multiplied by the estimated expected group size Ê(s) to obtain density of individuals $\widehat{D}$, and this estimate is multiplied by the surface area of each survey stratum to obtain the corresponding abundance estimate of dolphins by stratum ($\widehat{N}$). Overall density for the study area per year was obtained by calculating a mean of stratum estimates weighted by stratum area.

The Distance 6 software (Thomas et al., 2010) was used to analyze the data. The on-effort observations of Irrawaddy dolphin groups made from the line transects (Figure 2) were used for the distance sampling analysis. A stratified (by stratum or year) or pooled data approach was considered in fitting the detection function. Various combinations of key functions and adjustment term were considered to model the detection function (e.g., uniform + cosine or simple polynomial, half-normal + cosine or simple polynomial, hazard rate + cosine, or hermite polynomial). Goodness of fit tests were used to identify violations of assumptions. Exploratory analyses were conducted to examine options for truncation and grouping intervals to improve model fit for the detection function. Akaike's Information Criterion adjusted for small sample size (AICc) was used in final model selection. Encounter rate was estimated within each of the survey strata per year and its variance was estimated empirically using the replicate transect lines as samples. There may be a tendency for smaller dolphin groups to be missed more often than larger groups at large distances from the transect line, which can lead to “size bias” if the average group size is simply used during the estimation process. To test for bias in the estimate of group size, we applied a statistical hypothesis test at the 15% α−level to the regression of natural logarithm of group size against the probability of detection at distance x from the line within the Distance software. If the regression was statistically significant the expected group size [E(s)] was used, otherwise average group size was used to estimate density and abundance. Group size estimation was also stratified by survey stratum and year. Individual Irrawaddy dolphin density per stratum for each year and between sequential years was tested for statistically significant difference at the 5% significance level using a two-sided t-test (Buckland et al., 2004). This t-test explicitly accounts for the lack of independence in the data that went into the densities being compared due to using a common detection function across strata and years.

Results

Table 1 summarizes the numbers of sightings and species for each year. We had between 45 and 83 on effort sightings of dolphins each year, which included between 151 and 341 animals. The geographic distribution of sightings for each year distributed across the strata are in Figure 2A (2008 and 2009), Figure 2B (2012 and 2013) and Figure 2C (2014). Even with all years combined, we did not have enough sightings of Indo-Pacific humpback dolphins or Indo-Pacific finless porpoises to fit a detection function to obtain an accurate abundance estimate. The encounter rate for Indo-Pacific humpback dolphins, for example, was 0.06 sightings/km⁻¹ of effort.

TABLE 1

Table 1. Sightings and numbers of Irrawaddy dolphins seen in 5 years of surveys along the eastern Gulf coast of Thailand.

The total effort per stratum and year for Irrawaddy dolphins are detailed in Table 2. In the final models, data were pooled across survey strata and years and grouped into five equal-spaced intervals with right truncation at 450 m (10% of the data). Pooling provided a more robust detection function (see Figure 3) due to some sample size issues when stratifying per year or survey stratum, and also due to issues with the data measurements. In the early years there was a heaping of angle estimates at zero which indicates that particularly small angle sizes were not being measured accurately. In the later years it seemed that observers may have been overcompensating as there were more observations than expected some distance from the line (with no movement of dolphins away from the observers before measurements were taken).

TABLE 2

Table 2. Details of the total effort (L) per year in each survey stratum.

FIGURE 3

Figure 3. Detection functions fitted to the perpendicular distances of observations of groups of Irrawaddy dolphins. On-effort sightings were pooled across survey strata and survey years. Data were grouped for final analysis using six equal-spaced intervals with right truncation at 450 m.

The final model was a half-normal with cosine adjustment terms, which gave a detection probability of about 38% and an effective half strip width of 171.26 m (see Figure 3). Estimates of encounter rate and expected group size for the Irrawaddy dolphins and survey stratum are also detailed in Table 2. Based on the t-test p-value being smaller than the specified significance level of 15%, there is some indication of “size bias” in the North (p = 0.113) and Middle (p = 0.124) strata in 2009 and in the South (p = 0.125) in 2012, so the expected group size was used in those cases and the average group size for the remainder of the stratum-year combinations. The final estimates of Irrawaddy dolphin group and individual density, and abundance for each survey stratum per year and overall per year is shown in Table 3. Although there were differences between the strata per year and overall by sequential survey years, given the fairly high variance associated with the estimates, individual Irrawaddy dolphin densities overall were only significantly lower in 2012 compared to 2009. Only when considering one-tailed t-test results was the South stratum significantly lower than the Middle stratum in 2009, and the South stratum was also significantly lower than the North stratum in 2013.

TABLE 3

Table 3. Estimates of density (Ḋ) in number/km² (group density ${\widehat{D}}_s$in parentheses) and abundance ($\widehat{N}$) of Irrawaddy dolphins for each survey stratum per year and overall per year with their corresponding 95% confidence intervals (95% CI), and the percent coefficient of variation (%CV).

Discussion

The average relative abundance estimate of 423 Irrawaddy dolphins within 12 km of the coast reflects the estimate of animals in our survey area based on the number of sightings averaged over the 5 years (Table 3). Averaged over these years, based on our sighting patterns, the top and middle strata had slightly more sightings and groups of animals, and the bottom strata the least, with the exception of 2012 (Table 3). During this year there was increased fishing activity near the port of Khlong Yai. Now that we have an abundance estimate, the next step is to continue to monitor the population for trends; to see whether the numbers increase or decrease or remain the same over the next 5 years. Setting up the field methods and obtaining these estimates is a first step—knowing the population trends will provide us with a clearer idea of what the long-term prospects are for this species and whether conservation activities are effective.

Compared to other transect-based abundance estimates of coastal Irrawaddy dolphins in Southeast Asia, our present estimate is relatively large. A comparable project in the region is a 2 year line transect survey with similar methods for Irrawaddy dolphins, conducted in Sarawak, Malaysia in 2010 and 2011. The population estimate for this area was 129 dolphins, but included a river which contributed most of the sightings. The density of animals in coastal areas averaged 0.279 per km², in contrast to our average density of 0.982 per km² (Minton et al., 2013). Smith et al. (2004) surveyed a geographically isolated group of Irrawaddy's in the Philippines in 2001 and estimated an overall abundance of 77 animals. Research on coastal Irrawaddy's in the region is irregular and fragmented. Dolar and her collaborators have been investigating Irrawaddy dolphins in the Philippines and have recently discovered their presence in previously undocumented locations (Hines et al., in press). Kuit et al. (2014) are researching coastal dolphins in the Matang estuary of western Malaysia, but have not published abundance statistics. Kreb and Lim (2009) have estimated between 68 and 79 Irrawaddy dolphins are in Balikpapan Bay, in eastern Kalimantan, Indonesia. For a complete report on Irrawaddy dolphin presence and research throughout Southeast Asia, see Hines et al. (in press).

Despite having once been considered a common area of Irrawaddy dolphin occurrence (Stacey, 1996), few dolphins were seen in the islands west of the Trat coast and no dolphins were observed during a January 2014 survey in Chanthaburi and Rayong Provinces (Hines et al., 2013, 2014) (Figure 1). Modeling is underway to ascertain variations in environmental covariates and human use to help explain this marked difference in sightings. For now, the presence of so many dolphins is an indication that the Trat coast contains critical habitat for coastal Irrawaddy dolphins. We are working with the Thai Department of Marine and Coastal Resources (DMCR) on a long-term project to plan protective management areas.

We still need more data from nearby coastlines to determine the range of this population group. In Thailand, sightings of between 20 and 25 individuals were found by Tongnunui et al. (2011) in the Bang Pakong Estuary, approximately 250 km north of our fieldsite. We would recommend stable isotope analysis and photo-identification research to see if these animals mix with the dolphins we have seen in Trat. The Trat dolphins could also travel into the northern coast of Cambodia. In 2004, while on aerial surveys along the Cambodian coast, Hines et al. (2004) saw Irrawaddy dolphins on the northwestern coast near the Thai border. They had 24 sightings of approximately 79 dolphins, with a maximum group size of 15. There have been reports of Irrawaddy dolphins in southwestern Vietnam, close to the Cambodian border (Vu pers.comm). Coordination of efforts, particularly photo-identification, between scientists in Thailand, Cambodia and Vietnam is further needed to determine dolphin movement and habitat use across borders.

Over 5 years of research we were successful in creating a practical and repeatable systematic survey that allows for quantitative statistical analysis and long-term monitoring of the Irrawaddy dolphin population. Enough Irrawaddy dolphins were seen in the combined years for robust statistical analysis, with fewer issues in the sample data in later years, which shows the increasing skills of the international and Thai scientists trained in these methods. Also critical, each year the visibility of the scientists and our research increased conservation awareness in local villages. We stayed in local hotels run by villagers for all 5 years, hired a driver who is an active community member and conducted our research on a local fishing boat. We have given presentations and lectures at elementary schools in Trat Province, attended village council meetings and explained our research and concerns about cetacean bycatch and plastic pollution. Local teachers and students came on our boats and assisted with our fieldwork, and we worked with a local conservation group to take samples and teach about incidental bycatch in a local village after bycaught animals were found both on several beaches and floating in the water during our surveys.

This is a critical first step, however we still have important questions: What are population trends in this group of animals? What are changes in foraging and habitat patterns in different seasons, and years? What is the role of environmental covariates in distribution? One of our biggest questions is the possible change of foraging and habitat patterns in various seasons. Habitat modeling is needed to analyze relationships between sightings of dolphins, possible influences of varying riverine input and land use, and other environmental variables, such as temperature, salinity, distance to river mouths, and number/type of fishing vessels. Based on increased tourism and a growing coastal population, recommended research includes an assessment of threats, such as bycatch, plastic trash in the water, coastal development, pollution from groundwater runoff, and overfishing. Our goal is to continue to monitor this area with transect surveys every 5 years.

Although the abundance of dolphins in Trat is comparatively large, is this a sustainable population? The number of animals recently caught in nets is high compared to the abundance estimate, as evidenced by the bycatch we encountered during our years in the field. Between 2002 and 2013, 84 Irrawaddy dolphins have been found stranded in the eastern Gulf of Thailand (Teh et al., in press). This number, a probable underestimate, as not all bycaught animals are found, averages 10.5 dolphins per year. One method commonly used by marine mammal scientists to estimate if anthropogenic mortality is sustainable is the potential biological removal (PBR) (Wade, 1998). The equation,

$\text{PBR}={\text{N}}_{\text{min}}\frac{1}{2}{\text{R}}_{\text{MAX}}{\text{F}}_{\text{R}}$

is based on N_min, the minimum population estimate, ½R_MAX, half of the maximum theoretical net productivity rate of the population group (the default for cetaceans is 0.04; Wade, 1998), and a recovery factor F_R. After Whitty (2014), we used 0.1, 0.5, and 1. Using the average population estimate of 423, PBR ranges from 0.85 (F_R = 0.1), to 4.23 (F_R = 0.5), to 8.46 (F_R = 1). Wade (1998) concluded that an F_R of 0.5 was least biased. An underestimated average of 10.5 bycaught dolphins per year is over twice the calculated PBR of 4.23. Such a large estimate of bycatch is unsustainable and could lead to the depletion of this population (Wade, 1998). These calculations could be used as the basis for goals in bycatch management. This issue is common, and reflects the important threat of marine mammal bycatch, identified as a serious regional problem during the recent Southeast Asian Marine Mammal Workshop (Hines et al., in press).

Another question is how education and environmental change are shifting the way that local fishers see and value their environment and the role of these top predators, and how their ideas of conservation and stewardship are changing. Values can change as the result of various factors, such as the perception of threats and scarcity, political and economic circumstances, community cohesion and pressures, generational memories, and exposure to media. Marine mammals have a living presence in the lives and imaginations of the communities where they are seen year after year. These associations between wildlife and humans are especially valuable, as it is only through local solutions, and with local cooperation that these animals can survive.

Our close collaboration with the Thai DMCR has enabled us to create a good working relationship with local scientists. This has enabled our work to be meaningfully applied in management planning. The long-term nature of this project has brought local and national attention to these marine mammals and the threats they face. Incidents of bycatch are featured in national media, and are communicated widely by local conservation organizations. DMCR scientists and Directors concerned are convinced that protected area zoning and increased protection from bycatch are needed, and have begun pressing for conservation planning. The Thai government has begun talks with Cambodia about a transboundary marine protected area that would include areas in both countries where coastal Irrawaddy dolphins are found.

Author Contributions

All authors have made substantial contributions to the conception and design of the work, and the acquisition and interpretation of these data. All authors were involved in drafting and revising this work, approving it for publication, and agree to be accountable for the accuracy and integrity of the work.

Conflict of Interest Statement

The authors declare that the research was conducted in the absence of any commercial or financial relationships that could be construed as a potential conflict of interest.

Acknowledgments

This research was conducted with the approval of the Institutional Animal Care and Use Committee of San Francisco State University. We would like to thank the National Research Council of Thailand for their cooperation and support through the national permitting process. Many scientists from the DMCR joined this project over the years and made it possible. We apologize that we do not have room to name you all! We acknowledge Ocean Park Conservation Foundation and the Indo-Pacific Cetacean Research and Conservation Fund for grants that enabled this project. Our work in Thailand was always supported by Kanjana Adulyanukosol, whose visits to our boat were so wonderful. We miss you. Many thanks to Tara Whitty, Satoko Kimura, Long Vu, Hoang Minh Duc, Cindy Peter and Isabelle Groc. Our volunteers were Michael Yuen, Jennifer Siu, Laura Morse, Jen McGowan and Andrea Dransfield. Our research vessel was driven beautifully each year by Captain Leigh and his son Aa. Pi Hom, our driver, is a community member dedicated to marine conservation who was instrumental to our work.

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