1Co-editor, Griffith School of Environment, Griffith University, Nathan, Qld, 4111, Australia
2Co-editor, CMS Scientific Council, Queensland Turtle Research, P.O. Box 541 Capalaba, Qld 4157, Australia
Effective management of marine species has been challenging in part because of the cryptic nature of diverse life stages and the complexity of aquatic dispersal that is mediated by oceanographic features. This makes it difficult to define population boundaries or to understand population dynamics, particularly for marine migratory species where knowledge of migratory routes and population interactions during different life stages can be difficult to elucidate. Because of this, management for conservation of marine species has often taken place without the knowledge of exactly what is being managed. Are aggregations of individuals part of a single isolated population, a complex metapopulation, or do they come from a collection of independent populations that only share foraging habitats or migratory corridors? As our ability to define marine populations has improved through linking mark-recapture techniques, population genetics, satellite telemetry and isotope studies to oceanographic data, so too has the need to apply these findings to conservation management.
Conservation of marine turtle populations relies on being able to define populations and understand the geographic extent of habitat use throughout individual life history phases that may include oceanic or benthic developmental habitats, and extensive individual, population and species-level variation in the size and location of foraging home ranges and subsequent adult breeding migrations. To understand and manage populations requires determining whether a population nests at a single beach or island, or nests at multiple beaches. From an ecological perspective, populations are considered to be functionally independent, such that demographic processes are mostly independent of other populations and there is limited gene flow among different populations (Palsbøll et al., 2007). Populations are often comprised of sub-populations that are typically recognised as different spatial or temporal groupings of individuals. Examples of this include the many distinct rookeries that comprise the Northwest Shelf green turtle population (Dethmers et al., 2006) or the western Pacific leatherback population that nests across sites in Indonesia, Papua New Guinea, and the Solomon Islands, and shows behavioural differences in foraging behaviour among summer and winter nesting groups (Dutton et al., 1999; Benson et al., 2011). Continued gene flow among sub-populations is at a high enough level that sub-populations share demographic features and are not distinguished genetically.
From the perspective of conservation management, populations are also considered to be groupings of animals that function independently in the near term (tens or hundreds of years) and can thus be thought of as ‘Management Units’ (MU) or ‘genetic stocks’ (Moritz, 1994). Use of these terms, as well as the terms ‘population’ and ‘sub-population’, can be problematic due to different usage, thus it is necessary to clarify what is meant. In the IUCN Red List process, ‘population’ is defined to mean the entire taxon (species) and, more specifically, the definition only considers adults that are contributing to future generations (IUCN, 2010). What ecologists would consider as populations are instead defined as ‘sub-populations’ within the IUCN Red List assessments (IUCN, 2010). The term ‘stock’ can be problematic as it is often used in fisheries management to represent different geographic aggregations of fish that are commercially fished, without regard to whether they constitute a single population or mixed populations that share a feeding ground (Carvalho & Hauser, 1994). With regard to marine turtle populations, the term ‘Regional Management Unit’ (RMU) has been introduced for the purpose of setting conservation priorities (Wallace et al., 2011), yet the units that are defined are often inconsistent with a Management Unit (Moritz, 1994) approach (FitzSimmons, In Press). For the purposes of this paper, the terms population, Management Unit, and genetic stock are considered to be synonymous and the basis for effective marine turtle conservation management.
Several Management Units have been defined for marine turtles within the Indo-Pacific (e.g., Dethmers et al., 2006; Bourjea et al., 2007; Pittard, 2010). The location of foraging grounds and migratory routes are known for some genetic stocks (e.g., Benson et al., 2011), but many knowledge gaps remain. Because of limited tissue sampling for genetic studies, there are genetic stocks yet to be identified and additional sampling is needed to determine the geographic range of rookeries used by each genetic stock. For example, the defined green turtle genetic stock for Papua New Guinea, was based on a single location in the northeast at Long Island (Dethmers et al., 2006), but further research by Velez- Zuazo et al. (2006) showed that this stock extended a further 2000 kms westward to include rookeries off the northwest coast of Papua, Indonesia. Mark-recapture tagging studies have provided considerable information on the habitat range of genetic stocks (Limpus, 1997) and the use of satellite telemetry has been a valuable source of data on populations, particularly where there are limited mark-recapture records (e.g., Lushci et al., 2006; Benson et al., 2011). Genetic analyses of foraging aggregations of turtles have added to this knowledge by providing estimates of the proportional representation of genetic stocks at different foraging areas (Dethmers et al., 2010; Jensen, 2010; Nishizawa et al., 2013), but the efforts required to sample sufficient numbers of turtles at foraging grounds means that few studies have been conducted to date. These studies are particularly valuable if there are substantial levels of mortality at foraging areas as it allows the proportional assignment of mortality to the different genetic stocks that share the feeding ground (Jensen et al., 2010).
This paper aims to summarise the present state of knowledge for all species of marine turtle populations within the Indo-Pacific in terms of the distribution of rookeries, the relative size of rookeries, and how rookeries are grouped into genetic stocks. Information on the international extent of foraging areas or migratory routes is provided from mark-recapture data, satellite telemetry data, or genetic studies that indicate a genetic stock uses habitat across international borders. Data are provided as species-specific maps to show the locations of genetic stocks and to identify areas where there are knowledge gaps. This paper has been also been provided to the secretariat of the Indian Ocean South East Asia Memorandum of Understanding (IOSEA) to be included on the website (http://www.ioseaturtles.org/) and updated periodically with input from IOSEA affiliates.
Rookery location and estimated rookery size were taken from the published literature, unpublished reports, theses, conference proceedings, and personal communications from researchers throughout the Indo-Pacific. These data have been generated using GIS software (ArcView) and used to construct the maps shown in Figures 1-6. In these Figures, nesting locations are shown as dots that denote recorded nesting sites. The size of the dot is scaled, with the smallest dots representing 1-10 nesting females per year to the largest dots representing tens of thousands of females per year for Caretta caretta, Chelonia mydas and Lepidochelys spp., or thousands of females per year for Dermochelys coriacea, Eretmochelys imbricata and Natator depressus. Crosses denote recorded nesting sites for which the size of the nesting population has not been quantified. Nesting sites demonstrated to be a part of the same genetic stock are encircled and the abbreviated name of the genetic stock is identified (see Table 1).
Designations of genetic stocks were taken from the published literature, unpublished reports, theses and conference proceedings. In all cases, these studies used a definition of genetic stocks following the Management Unit (MU) concept as provided by Moritz (1994). Following Moritz (1994), marine turtle MUs are recognised by having significant allele frequency differences, such as observed in mitochondrial (mt) DNA haplotype frequencies (e.g., Dethmers et al., 2006), nuclear microsatellite allele frequencies (e.g., FitzSimmons et al., 1997b), or SNPs (single nucleotide polymorphisms) allele frequencies (e.g., Roden et al., 2013). If the null hypothesis that sampled rookeries have the same mtDNA haplotype frequencies cannot be rejected, then they are considered as being grouped into the same genetic stock. If the null hypothesis is rejected when comparing two rookeries, or groups of rookeries, then they are designated are separate genetic stocks. This is done on the basis that significant genetic differentiation indicates limited gene flow and that populations are thus expected to function with demographic independence (Moritz, 1994; Palsbøll et al., 2007). Data from mtDNA are particularly useful for conservation management of marine turtle populations because the matrilineal inheritance of the mtDNA means that the data reflect the history and relationships among rookeries (Avise, 1995). Application of nuclear genetic markers (microsatellites and SNPs) can be beneficial for understanding male-mediated gene flow among populations and male migratory behaviour relative to females. When used in regional studies, they have contributed to the designation of genetic stocks, mostly with similar results (FitzSimmons et al., 1997b; Pittard, 2010; Roden et al., 2013).
In total, 57 genetic stocks have been identified for all species of marine turtles within the Indo-Pacific, but many regional or species-specific gaps remain (Tables 1-2, Figures 1-6). For 37 (65%) of these stocks, some habitat use outside of the country(s) where the rookeries are located have been identified through tag recovery data, satellite telemetry data, or genetic stock analyses. International habitat use by various genetic stocks was recorded for all species, emphasising the need for international cooperation in marine turtle conservation efforts. The designated genetic stocks represent not only the demographicallyindependentmarineturtlepopulations within the Indo-Pacific, they also represent unique combinations of genetic diversity within the region.
Five genetic stocks of loggerhead turtles have been identified (Table 1, Figure 1) in the Indo-Pacific (Hatase et al., 2002; Shamblin et al., 2014). At present, genetic studies of the southwest Pacific stock do not uncover any differences between rookeries in eastern Australia and New Caledonia (FitzSimmons et al., unpubl. data), although tagging of females suggests that these regions function as independent populations (Limpus, 2008a). Frequency differences among mtDNA haplotypes distinguish rookeries in Japan, eastern and western Australia as forming three unique populations, though the level of divergence among mtDNA haplotypesin the eastern Indian Ocean and western Pacific Ocean is low. Only one shared haplotype, found in one turtle in Japan, has been observed in both Australia and Japan (Hatase et al., 2002). In contrast, there is high genetic divergence between the Japan/Australia/New Caledonia genetic lineages and the highly divergent Oman and South Africa lineages (Shamblin et al., 2014). Additional sampling is needed for the southwest Pacific Ocean and to determine whether the Sri Lanka rookeries form an additional genetic stock, and to clarify whether rookeries in Yemen are part of the northwest Indian Ocean stock.
Genetic analyses have been conducted on some loggerhead turtle feeding ground samples, stranded turtles and turtles caught by fisheries. This includes feeding grounds in Western Australia and Queensland (Pacioni et al., 2012, unpubl. data), stranded turtles in Australia (FitzSimmons et al., unpubl. data), and fisheries bycatch samples in Peru (Boyle et al., 2009). The latter study confirmed an hypothesis that loggerhead turtles from rookeries in eastern Australia and New Caledonia are traversing the south Pacific and are caught by long-line fisheries off the coast of Peru.
Green turtles have the largest number of genetic stocks identified within the Indo-Pacific, with 30 different stocks designated to date (Figure 2). This reflects a high level of genetic diversity found in the region, including at least five divergent genetic lineages (Dethmers et al., 2006; Bourjea et al., 2007). Dethmers et al. (2006) analysed 27 rookeries and determined there were 17 management units among sample sites in the western Indian Ocean, SE Asia and western Pacific. The Scott Reef genetic stock (Dethmers et al., 2006) has been expanded to include Browse Island (Jensen, 2010) and the genetic stock identified from Long Island in northeast Papua New Guinea has been expanded to include all of northern New Guinea (Velez-Zuazo et al., 2006). Research by Mahardika et al. (2007) suggests that the northeast Borneo and east Borneo genetic stocks, identified by Dethmers et al. (2006) as the SE Sabah and Berau Islands management units, may constitute a single genetic stock, although work by Arshaad & Kadir (2009) supports the designation of at least two stocks. In the southwestern Indian Ocean, Bourjea et al. (2007) identified four genetic stocks that include the Arabian Peninsula, the northern Mozambique Channel, Europa and Juan de Novo. There is some evidence that there may be additional genetic differentiation within the genetic stock of the northern Mozambique Channel, but further sampling in the region is required (Bourjea et al., 2007).
Regional genetic studies have identified additional genetic stocks in the Indo-Pacific. These include genetic stocks at Coburg Peninsula in the Northern Territory, Australia and the Cocos (Keeling) Islands (Jensen, 2010). In the northwestern Pacific and South China Sea, three genetic stocks have been identified to exist in Japan, southeast Taiwan and southwest Taiwan (Cheng et al., 2008; Nishizawa et al., 2011). Genetic differentiation identified two stocks in Taiwan, which was somewhat unexpected, given the two island rookeries are only ~250 km distant from each other. However, a similar result of genetic differentiation was found between the Ashmore Reef and Scott/Browse genetic stocks in the Arafura Sea, which are comprised of island rookeries ~225 distant (Dethmers et al., 2006; Jensen, 2010). Most surprisingly, there was a high level of genetic differentiation (no haplotypes were shared between the sites) between the Taiwan stocks, although the sample size was small (n = 14) for one site and additional sampling is needed. The most striking result was found by Nishizawa et al. (2011), who uncovered mtDNA genetic differentiation between rookeries on two islands in Japan where sample sites were located only 40 – 60 kms apart. They recommended further study to confirm this, so these rookeries are considered a single stock at present. In contrast to these geographically limited genetic stocks, the North West Shelf stock in Western Australia encompasses over 1000 kms between the furthest rookeries sampled (Dethmers et al., 2010) and the northern New Guinea stock includes rookeries over 2000 kms apart (Velez-Zuazo et al., 2006).
Genetic studies of rookeries in Thailand did not find significant genetic divergence between rookeries at Khram Island in the Gulf of Thailand and Huyon Island in the Andaman Sea (Kittiwattanawong et al., 2003), even though these are separated by >2300 kmof coastline. It was suggested that these results could be due to low levels of gene flow through the Malacca Straits after colonisation by a common ancestor (Kittiwattanawong et al., 2003). This explanation is problematic given that each of the rookeries is genetically divergent from the intermediately located Peninsular Malaysia stock. Satellite telemetry of post-nesting turtlesshows behavioural differences between the two rookeries in the location of their foraging grounds (Kittiwattanawong et al., 2002, 2003; Kittiwattanawong & Manansap, 2009), suggesting demographic independence of the two rookeries, although additional telemetry data are needed. As suggested, a lack of genetic differentiation can occur when populations are colonised from the same ancestral population, and too few generations have occurred to develop differentiation through genetic drift and new mutations (Avise, 2000). Alternatively, genetic similarities may reflect the random nature of colonisation from multiple source populations that result in demographically separate populations appearing to be similar. The most common haplotype in Thailand rookeries is shared among all rookeries throughout the region, the second most common haplotype is observed in several Malaysian stocks and none of the other six haplotypes observed at lower frequencies are shared between the two Thailand rookeries. Colonisation of the Sunda Shelf in the last 8,000 years as sea levels dropped would have occurred from multiple source populations, which could have led to the Thailand rookeries appearing to be similar, as suggested for loggerhead populations on the east and west coast of Florida (Encalada et al., 1998). A similar situation of no observed genetic divergence occurs between two hawksbill populations in Australia (nQLd, neA; Table 1), but due to differences in nesting seasonality, they are considered as separate genetic stocks (Limpus, 2009a). We provisionally consider the two rookeries sampled in Thailand as separate stocks based on behavioral differences in foraging locations (Kittiwattanawong & Manansap, 2009) and their differentiation from the Peninsular Malaysia stock.
Mixed stock analyses of mtDNA data have been conducted for several green turtle foraging grounds in the Indo-Pacific to determine the proportional contribution of different genetic stocks to shared foraging grounds. Foraging grounds have been analysed in the southwest Pacific Ocean (Jensen, 2010; Read et al., In Press), northwest Pacific Ocean (Nishizawa et al., 2013), western Indian Ocean (Jensen, 2010), Arafura and Timor seas (Dethmers et al., 2010), South China Sea (Jensen, 2010) and the Celebes Sea (Mahardija et al., 2007). Considerable variation in results exists, with some foraging ground aggregations being composed mostly of turtles from the nearest genetic stock (i.e., Aru, Gulf of Capentaria, nGBR; Dethmers et al., 2010; Jensen, 2010) while other aggregations include significant numbers of turtles from genetic stocks over 1,000 km distant (i.e., New Caledonia and Japan; Nishizawa et al., 2013; Read et al., In Press). Unfortunately, the presence of a high proportion of shared mtDNA haplotypes in the Indo- Pacific often preludes firm conclusions about the origins of turtles at foraging grounds. Instead, most knowledge on the international dispersal of post-nesting turtles has come from tag recovery data (Table 1 references). Genetic analyses have been conducted on green turtles harvested in Bali and Australia (Moritz et al., 2002), demonstrating that the Bali harvest harvests turtles from a broad geographic region and includes turtles originating from other counties, whereas the nGBR harvest primarily has a local impact (Moritz, 2002; Jensen, 2010).
Important knowledge gaps remain, with several large, isolated rookeries not yet analysed, and regions where additional sampling of rookeries would help clarify stock boundaries (see Figure 2). Additional green turtle genetic stocks are likely to be found in the Indo-Pacific, particularly if the rookeries are located more than 500 km from rookeries used by other genetic stocks (Dethmers et al., 2006). Mixed stock analyses of feeding grounds will require large sample sizes (Jensen, 2001) and will be most effective if conducted as regional transects (e.g., Dethmers et al., 2010; Jensen, 2010) that incorporate knowledge of the complex ocean currents of the region.
Population genetic studies have identified three genetic stocks in the Indo-Pacific, but many gaps remain in the sampling of low-density rookeries throughout the region. Stocks are identified in the southwest Indian Ocean, northeast Indian Ocean (Malaysia, Nicobar Islands) and western Pacific Ocean (Dutton et al., 1997, 2007; Shanker et al., 2011) (Table 2, Figure 3). The grouping of Malaysia and Nicobar is tentative as it is based on only nine samples from Malaysia (Dutton et al., 1999) and there is some evidence that they forage in different areas (Limpus, 1997; Shanker, pers. comm. 2014, data at seaturtle.org/stat/). Additional sampling is needed in many areas to determine the boundaries of the nesting regions for each stock. Satellite telemetry has revealed the extensive foraging range of the western Pacific Ocean stock, with differential migratory behaviour observed between austral summer and winter nesting turtles (Benson et al., 2011). Although it is speculated that demographic differences may exist between austral summer and winter nesting turtles, nesting throughout the year among western Pacific Ocean turtles would allow for sufficient gene flow such that the stock is considered a meta-population (Benson et al., 2011). Ongoing satellite telemetry of post-nesting females from the northeast Indian Ocean stock is similarly demonstrating a wide dispersal of individuals to foraging areas in several countries (Shanker, pers. comm. 2014, data atseaturtle.org/stat/) and suggests the origins for at least some of the stranded leatherback turtles along the western Australia coast (Prince, 2004).
Population genetic studies of hawksbill turtles in the Indo-Pacific have revealed the presence of at least nine genetic stocks (Mortimer & Broderick, 1999; FitzSimmons, 2010; Arshaad & Kadir, 2009, Tabib et al., 2011, 2014). Interesting results include the possible separation of stocks within the Arabian Gulf and the grouping of distant rookeries in Seychelles and Chagos (FitzSimmons, 2010; Tabib, 2014). The Gulf of Thailand stock is proposed, but additional samples are needed to confirm this (Arshaad & Kadir, 2009). The north Queensland and northeast Arnhem Land stocks could not be differentiated with genetic analyses, but are separated on the basis of that the turtles in those populations nest at different times of year (Limpus, 2009a). There are severe knowledge gaps in the genetic study of hawksbill turtle rookeries throughout the Indo- Pacific (Figure 4). Foraging ground mixed stock analyses have been conducted for some areas (FitzSimmons, 2010), but most data on the use of foraging grounds across international borders comes from limited tag recovery data of post-nesting females (Table 1 references).
Separate genetic stocks have been identified in six regions that include the eastern India coast, Sri Lanka, Andaman and Nicobar Islands (India), Peninsular Malaysia, western Northern Territory (Australia) and western Cape York Peninsula (Australia) (Bowen et al., 1998; Shanker et al., 2004; Jensen et al., 2013; Shanker et al., 2011). Preliminary data from nesting turtles in Indonesia have been provided that suggest substantial variation from the Australian rookeries (I. B. W. Adnyana et al., unpublished data, reported in Jensen et al., 2013). Many important sampling gaps exist, particularly in Africa, Oman, western India, northeast Indian Ocean, the South China Sea, Arafura Sea and Timor Sea (Figure 5). As observed in other species, the geographic extent of genetic stocks is highly variable, such as the grouping of many rookeries along the eastern India coast into a single genetic stock, whereas turtles nesting in nearby in Sri Lanka are genetically differentiated into a separate stock (Shanker et al., 2004).
Information on the use of internationally dispersed foraging grounds by particular stocks is limited, given there are no published genetic studies of olive ridley turtles sampled at feeding grounds in the Indo-Pacific and few tag recovery records of turtles found outside of the countries they were tagged in. Jensen et al. (2013) analysed mtDNA variation in olive ridley turtles that had become entangled in discarded fishing nets (ghost nets) that drifted ashore in the Gulf of Carpentaria. It appears that the nets are entangling turtles from Australian and Indonesian stocks at shared feeding grounds in the Arafura Sea, and thus have a broad impact. Satellite tagging of post-nesting females from Northern Australia supports the hypothesis of shared feeding grounds, given that some tracked females entered Indonesian waters (Whiting et al., 2007). Considerably more genetic, tagging and satellite telemetry studies are needed to better understand the dynamics of olive ridley populations within the Indo-Pacific.
Five genetic stocks of flatback turtles have been identified (Pittard, 2010), all of which nest only within Australia (Table 1, Figure 6). Some of these stocks use feeding grounds in Indonesia and Papua New Guinea (Limpus, 2007). Within the eastern Queensland and Arafura Sea genetic stocks there is evidence of restricted gene flow among at least some pairs of rookeries that have been sampled (Pittard, 2010). Some rookeries may be more independent than can be uncovered by genetic studies at present. Additional sampling along the northwest coast of Western Australia Kimberley region will help determine the boundary between the winter nesting genetic stock sampled at Cape Domett (Joseph Bonaparte Gulf stock) and the summer nesting stock sampled at Eco Beach (southwest Kimberly stock).
Several satellite telemetry studies of post-nesting females are being conducted and reveal extensive migrations, mostly within Australian waters (see seaturtle.org/stat/).
Considerable progress has been made to define population boundaries and understand migratory behaviour of marine turtles within the Indo- Pacific, which has supported international efforts in conservation management. Genetic studies have led to the identification of 57 genetic stocks that are considered as separate management units in that the loss of nesting females in one stock will not be replaced readily by nesting turtles from another stock. Over two-thirds (68%) of the genetic stocks have turtles that either breed in more than one country, or breed and forage in different countries, thus international cooperation is critical for understanding and protecting marine turtle populations in the Indo-Pacific.
One important conclusion from population genetic studies is the inability to predict which rookeries are grouped together as a genetic stock, unless tagging efforts have been extensive and cover a large number of rookeries in a region. Stock boundaries have varied hugely, separating rookeries <60 kms distant, to the grouping of rookeries >2000 kms apart; thus filling in knowledge gaps needs to be quantitative, and cannot be assumed. Similarly, tagging and satellite telemetry studies of migratory turtles haveprovided important data on the broader geographic range of a stock at foraging locations and migratory pathways, but unless studies are extensive, it is not possible to quantify the extent to which stocks use different locations. Genetic studies using mixed stock analyses have provided quantification of how stocks are distributed in benthic as well as pelagic habitats. These studies have been particularly important in allowing quantification of stock-specific impacts from human disturbance, such as incidental capture in fisheries or directed take (Bowen et al., 1995; Jensen et al., 2012). One of the largest remaining gaps is the lack of understanding about the pelagic phase of post-hatchling and juvenile turtles in the Indo-Pacific, and genetic studies can provide important insights if samples can be obtained (e.g., Boyle et al., 2009).
Genetic stocks/Management Units versus Regional Management Units
Most of the designations of genetic stocks have been based upon rejecting a hypothesis that sampled rookeries share the same mtDNA haplotype frequencies. Palsbøll et al. (2011) argue that a more effective approach would be to set a threshold level of dispersal as the criteria for defining management units. For marine turtle genetic stocks, dispersal would relate to the number of females that migrate between two rookeries, or groups of rookeries, being analysed. From a genetic perspective, the question becomes not just whether two populations are genetically divergent, but by how much. The authors acknowledge however, that empirical links between dispersal and demographic independence are poorly known for most species (Waples & Gaggiotti, 2006), and that species- specific models linking demographic parameters and population genetic estimations are needed. Setting a threshold level of dispersal has been done for the identification of salmon stocks by the IUCN Salmon Specialist Group, who determined the appropriate threshold level to be less than one migrant per year. Theoretical analyses are needed to link a threshold level of dispersal to the equivalent level of genetic divergence as observed in genetic studies. For sockeye salmon (Onchorhynchusnerka) the threshold of one migrant per year was determined to equate to a genetic divergence of FST = 0.04 using nuclear microsatellite data (IUCN, 2014), where FST = 0 for identical populations and FST = 1 for populations that do not share any of the same alleles.If the same approach is taken for defining marine turtle stocks, then rookeries known to have (on average) one female per year that has switched between two rookeries, then these rookeries can be defined as part of the same genetic stock. To determine an FST threshold for defining marine turtle stocks requires establishing the relationships among dispersal, gene flow, generation time and genetic divergence using empirical data. At present, the designation of genetic stocks based upon rejecting a null hypothesis of no genetic divergence is likely to be a valid, and probably conservative, approach for defining marine turtle populations.
An alternate approach for defining ‘units’ for management, known as Regional Management Units (RMUs), was proposed by Wallace et al. (2010) and used for setting global conservation priorities (Wallace et al., 2011). In general, this approach does not take a population level perspective, but instead groups populations into regional constructs, largely based upon the sharing of foraging areas. While the RMU process aims to be informative by incorporating a variety of data sources and provides distribution maps of habitat use (Wallace et al., 2010), the resultant RMUs may comprise a single population, multiple populations, or unknown populations, thus it is not clear what is being managed. Within the Indo-Pacific 31 RMUs have been defined, which include eight putative RMUs where data were lacking (Wallace et al., 2010). In comparison to the 57 genetic stocks identified to date within the Indo-Pacific, and with the expectation that more will be defined, the RMU approach is clearly different. Olive ridley turtle populations are reduced from six genetic stocks (with more expected) to four RMUs, with a west Pacific RMU that includes the western Pacific, all of southeast Asia, Australia and the western Indian Ocean. Additionally, there are two northeast Indian RMUs that separate turtles based on whether or not they nest in arribadas (Wallace et al., 2010). Most of the seven hawksbill turtle RMUs are putative so do not bear scrutiny, but the five flatback turtle genetic stocks have been reduced to three RMUs (Wallace et al., 2010), one of which includes geographically distant stocks that nest at different times of the year. The biggest discrepancy is for green turtle populations in the Indo-Pacific; with 30 genetic stocks reduced to eight RMUs (Wallace et al., 2010). One RMU that stands out as inappropriate is the southwest Pacific RMU, which includes the New Caledonia, Coral Sea, southern Great Barrier Reef, northern Great Barrier Reef and northern New Guinea genetic stocks (Wallace et al., 2010). This includes stocks (sGBR, nGBR) that are highly genetically divergent and known to function with complete demographic independence, other than the sharing of feeding grounds in some locations (Limpus, 2008b). Because leatherback turtle genetic stocks tend to use several nesting beaches within a large region, and loggerhead turtle genetic stocks are quite isolated from each other, the RMU approach for these two species in the Indo-Pacific does not differ from a genetic approach, with the exception that the RMU approach presents putative stocks.
Rather than benefitting the local or regional management of marine turtle populations, the RMU approach has the potential in some areas and for some species to de-emphasise the importance of monitoring and managing from an ecologically sound population perspective. We argue for the need to maintain the focus of management at the level of the genetic stock because critically, nesting habitats used by a specific population (genetic stock, MU) would not readily be recolonised by migrants from other genetic stocks in the near term if local extinction occurs (Moritz, 1994; Palsbøll et al., 2007). Additionally, the distribution of genetic divergence in the Indo-Pacific emphasises the importance of prioritizing the conservation of genetic stocks, not simply based on the size of the stock, but also by the unique combination of genetic diversity found within genetic stocks. For example, some genetic stocks are known to only support tens of females per year while other stocks support tens of thousands of females, but from a biodiversity perspective they may be equally significant. For example, the much smaller non-arribada olive ridley populations of the Indo-Pacific contain more genetic diversity than the large arribada population in India (Shanker et al., 2004, 2011; Jensen et al., 2013).
Management for turtle conservation at a genetic stock level involves a two-step process of first identifying which rookeries group together to form a genetic stock, and then identifying the nearshore and oceanic habitat used by each population with a combination of genetic, tagging and telemetry data. This combined approach provides managers with the information needed to prioritise actions based on threats to nesting beaches and feeding grounds for each population. It also provides more specific information to be used when negotiating internationally regarding these shared populations. Rather than relying on the RMU maps given in Wallace et al. (2010), countries should develop maps for each genetic stock indicating rookery locations and habitat use in pelagic and benthic environments. This has recently been done in Australia for incorporation into a revised marine turtle recovery plan. For the advancement of marine turtle conservation and management in the Indo- Pacific, we urge the continued progress in delineating marine turtle genetic stocks in the Indo-Pacific and using that informationas the basis for targeting further research, monitoring and international collaboration to achieve better management outcomes for marine turtles.
Adyana, W, L.P. Soede, G. Gearheart& M. Halim. 2008. Status of green turtle (Chelonia mydas) nesting and foraging population of Berau, East Kalimantan, Indonesia, including results from tagging and telemetry. Indian Ocean Turtle Newsletter 7: 2-11.
Adyana, W, L.P. Soede & M. Halim. 2009. Satellite telemetry and tagging activities of sea turtles in Indonesia. In: Report on the Third Technical Consultation on Research for Stock Enhancement of Sea Turtles (Japanese Trust Fund IV Program) (eds. Kadir, S.A.S.A. & O. Abe)SEAFDEC-MFRDMD/RM/24: 43-51.
Alfaro-Shigueto, J., P.H. Dutton, J. Mangel & D. Vega. 2004. First confirmed occurrence of loggerhead turtles in Peru. Marine Turtle Newsletter 103: 7–11.
Arshaad, W.M. & S.A.S.A. Kadir. 2009. Identification of the stock/population of green and hawksbill turtles in the Southeast Asian region.In: Report on the Third Technical Consultation on Research for Stock Enhancement of Sea Turtles (Japanese Trust Fund IV Program) (eds. Kadir, S.A.S.A. & O. Abe) SEAFDEC-MFRDMD/RM/24:25-135.
Avise, J.C. 1995. Mitochondrial DNA polymorphism and a connection between genetics and demography of relevance to conservation. Conservation Biology 9: 686-690.
Avise, J.C. 2000. Phylogeography the History and Formation of Species. Harvard University Press, Cambridge MA, USA.
Baldwin R., G.R. Hughes & R.I.T. Prince. 2003. Loggerhead turtles in the Indian Ocean. In: Loggerhead Sea Turtles. (eds. Bolten A.B. & B.E. Witherington). Pp. 218–232. Smithsonian Institution, Washington D.C., USA.
Bali, J., H-C. Liew, E-H. Chan & O.B. Tisen. 2002. Long distance migration of green turtles from Sarawak Turtle Islands, Malaysia. In: Proceedings of the Twentieth Annual Symposium on Sea Turtle Biology and Conservation (comps Mosier, A., A. Foley & B. Brost). NOAA Technical Memorandum NMFS-SEFSC-477:32-33.
Benson, S.R., T. Eguchi, D.G. Foley, K.A. Forney, H. Bailey, C. Hitipeuw, B.P. Samber et al. 2011. Large-scale movements and high-use areas of western Pacific leatherback turtles, Dermochelys coriacea. Ecosphere 2: art84. doi:10.1890/ ES11-00053.1
Bourjea J., S. Lapégue, L. Gagnevin, D. Broderick, J.A. Mortimer, S. Ciccione, D. Roos et al. 2007. Phylogeography of the green turtle, Chelonia mydas, in the Southwest Indian Ocean. Molecular Ecology 16: 175-186.
Bowen, B.W., A.B. Meylan, J.P. Ross, C.J. Limpus, G.H. Balazs & J.C. Avise. 1992. Global population structure and natural history of the green turtle (Chelonia mydas) in terms of matriarchal phylogeny. Evolution 46: 865-881.
Bowen, B.W., F.A. Abreu-Grobois, G.H. Balazs, N. Kamezaki, C.J. Limpus & R.J. Ferl. 1995. Trans-Pacific migrations of the loggerhead turtle (Caretta caretta) demonstrated with mitochondrial DNA markers. Proceedings of the National Academy of Sciences of the United States of America 92: 3731-3734.
Bowen, B.W., A.M. Clark, F.A. Abreu-Grobois, A. Chaves, H.A. Reichart & R.J. Ferl. 1998. Global phylogeography of the ridley sea turtles (Lepidochelys spp.) as inferred from mitochondrial DNA sequences. Genetica 101: 179-89.
Boyle, M.C., N.N. FitzSimmons, C.J. Limpus, S. Kelez, X. Velez-Zuazo & M. Waycott. 2009. Evidence for trans- oceanic migrations by loggerhead sea turtles in the southern Pacific Ocean as demonstrated by mtDNA sequence analysis. Proceedings of the Royal Society B 276: 1993-1999.
Broderick, D., H. Johanson, S. Lavery, J. Miller, & C. Moritz. 1998. Genetic Assessment of Western and Central Indian Ocean Marine Turtle Stocks. Final Report for the Department of Environment, Republic of Seychelles Government. 15 January 1988.
Carvalho, G.F. & L. Hauser. 1994. Molecular genetics and the stock concept in fisheries. Reviews in Fish Biology and Fisheries 4: 326-350.
Cheng, I.-J., P. H. Dutton, C.-L. Chen, H.-C. Chen & J.- W. Shea. 2008. Comparison of the genetics and nesting ecology of two green turtle rookeries. Journal of Zoology 276: 375-384.
De Silva, G.S. 1982. The status of sea turtles populations in east Malaysia and the South China Sea. In: Biology and Conservation of Sea Turtles (ed. Bjorndal, K.A.). Pp. 327- 337. Smithsonian Institution Press, Washington D.C., USA.
deVeyra, R.T.D. 1994. Foreign tag recoveries from the Philippines. Marine Turtle Newsletter 64: 6 -9.
Dethmers, K.E.M., D. Broderick, C. Moritz, N.N. FitzSimmons, C.J. Limpus, S. Lavery, S. Whiting et al. 2006. The genetic structure of Australasian green turtles (Chelonia mydas): exploring the geographic scale of genetic exchange. Molecular Ecology 15: 393-3946.
Dung, P.H. 2009. Review of sea turtle tagging and satellite tracking activities in Vietnam. In: Report on the Third Technical Consultation on Research for Stock Enhancement of Sea Turtles (Japanese Trust Fund IV Program) (eds. Kadir, S.A.S.A. & O. Abe) SEAFDEC-MFRDMD/RM/24: 95-100.
Dutton, P.H., B. W. Bowen, D.W. Owens, A.R. Barragan & S.K. Davis. 1999. Global phylogeography of the leatherback turtle (Dermochelys coriacea). Journal of Zoology 248:3 97- 409.
Dutton, P.H., C. Hitipeuw, M. Zein, S.R. Benson, G. Petro, J. Pita, V. Rei, L. Ambio & J. Bakarbessy. 2007. Status and genetic structure of nesting populations of leatherback turtles (Dermochelys coriacea) in the Western Pacific. Chelonian Conservation and Biology 6: 47-53.
Encalada, S.E., K.A. Bjorndal, A.B. Bolten, J.C. Zurita, B.A. Schroeder, E. Possardt, C.J. Sears et al. 1998. Population structure of loggerhead turtle (Caretta caretta) nesting populations in the Atlantic and Mediterranean as inferred from mitochondrial DNA control region sequences. Marine Biology 130: 567-575.
FAO 2006 (Food and Agriculture Organisation of the United Nations). 2006. Report on the workshop on assessing the relative importance of sea turtle mortality due to fisheries. Rome: FAO GCP/INT.919/JPN.
FitzSimmons, N.N. 2010. Population genetic studies in support of conservation management of hawksbill turtles in the Indian Ocean. Final Report Marine Turtle Conservation Award 98210-7-G126 to United States Fish and Wildlife Service, June 2010.
FitzSimmons, N.N. In Press. Management Units versus Regional Management Units: Dueling perspectives for conservation. In: Proceedings of the 32nd Annual Sea Turtle Symposium on Sea Turtle Biology and Conservation.
Indian Ocean Turtle Newsletter No. 20
NOAA Technical Memorandum NOAA NMFS-SEFSC- XXX: XXX.
FitzSimmons, N.N., C. Moritz, C.J. Limpus, J.D. Miller, C.J. Parmenter & R. Prince. 1996. Comparative genetic structure of green, loggerhead and flatback populations in Australia based on variable mtDNA and nDNA regions. In: Proceedings of the International Symposium on Sea Turtle Conservation Genetics, Sept. 12-14, 1995, Miami, Florida (eds. Bowen B and W. Witzel). U. S. Dept. of Commer. NOAA Tech memorandum NMFS-SEFSC-396:25-32.
FitzSimmons, N.N., A.R. Goldizen, J.A. Norman, C. Moritz, J.D. Miller & C.J. Limpus. 1997a. Philopatry of male marine turtles inferred from mitochondrial markers. Proceedings of the National Academy of Science 94: 8912-8917.
FitzSimmons, N.N., C. Moritz, C.J. Limpus, L. Pope & R. Prince. 1997b. Geographic structure of mitochondrial and nuclear gene polymorphisms in Australian green turtle populations and male-biased gene flow. Genetics 147: 1843- 1854.
Formia A., B.J. Godley, J.F. Dontaine & M.W. Bruford. 2001. Mitochondrial DNA diversity and phylogeography of endangered green turtle (Chelonia mydas) populations in Africa. Conservation Genetics 7: 353-319.
Frazier, J., Arauz, R., Chevalier, J., Formia, A., Fretey, J., Godfrey, M.H. Marquez et al. 2007. Human-turtle interactions at sea. In: Biology and Conservation of Ridley Sea Turtles (ed. Plotkin, P.T.). Pp. 253 – 295. The John Hopkins University Press, Baltimore MA, USA.
Gasperetti, J., A.F. Stimson, J.D. Miller, J.P. Ross & P.R. Gasperetti. 1990. Turtles of Arabia. Fauna of Saudi Arabia 13: 170-367.
Hamann M., R.L. Kamrowski & T. Bodine. 2013. Assessment of the conservation status of the loggerhead turtle in the Indian Ocean and South-East Asia. IOSEA Marine Turtle MoU Secretariat, Bangkok.
Hatase, H., M. Kinoshita, T. Bando, N. Kamezaki, K. Sato, Y. Matsuzawa, K. Goto, et al. 2002. Population structure of loggerhead turtles, Caretta caretta, nesting in Japan: Bottlenecks on the Pacific population. Marine Biology 141: 299-305.
Isnain, I. 2009. Terminal country report on tagging and satellite telemetry study: Sabah, Malaysia. In: Report on the Third Technical Consultation on Research for Stock Enhancement of Sea Turtles (Japanese Trust Fund IV Program) (eds. Kadir, S.A.S.A. & O. Abe).SEAFDEC- MFRDMD/RM/24:58-63.
IUCN (The International Union of the Conservation of Nature) Standards and Petitions Subcommittee. 2010. Guidelines for Using the IUCN Red List Categories and
Criteria. Version 8.1. http://intranet.iucn.org/webfiles/doc/ SSC/RedList/RedListGuidelines.pdf. Accessed 6 June 2014.
IUCN 2014. The IUCN Redlist of Threatened Species 2014.1 Onchorhynchus nerka. http://www.iucnredlist.org/ details/135301/0. Accessed 18 July 2014.
Jenson, M.P. 2010. Assessing the composition of green turtle (Chelonia mydas) foraging grounds in Australasia using mixed stock analyses. PhD Thesis, University of Canberra, Canberra, Australia.
Jensen, M.P., C.J. Limpus, S.D. Whiting, M. Guinea, K. Dethmers, I.B.W. Adyana, R. Kennett et al. 2013. Defining olive ridley turtle Lepidochelys olivacea management units in Australia and assessing the potential impact of mortality in ghost nets. Endangered Species Research 21: 241-253.
Kamarruddin, I. 1994. The status of marine turtle conservation in Peninsular Malaysia. In: Proceedings of the First ASEAN Symposium-Workshop on Marine Turtle Conservation. Manila (eds. A. Nacu, R. Trono, J. A. Palma, D. Torres and F. Agas Jr.). Pp 87-103. World Wildlife Fund.
Kapurusinghe, T. & R. Cooray. 2002. Marine turtle bycatch in Sri Lanka. Survey Report. Pandura, Sri Lanka: Turtle Conservation Project (TCP) Report. ISBN 955-8758-01-9.
Kelez, S., X. Velez-Zuazo. & C. Manrique. 2003 New evidence on the loggerhead sea turtle Caretta caretta (Linnaeus 1758) in Peru. Ecological Applications 2: 141–142.
Kittiwattanawong, K., S. Chantrapornsyl, W. Sakamoto & N. Arai. 2002. Tracking of green turtles Chelonia mydas in the Andaman Sea using platform transmitter terminals. Phuket Marine Biological Center Research Bulletin 64: 81-87.
Kittiwattanawong, K., S, Mananunsai, M. Kinoshita & K Nakayama. 2003. No genetic divergence between green turtle Chelonia mydas nesting populations from the Andaman Sea and the Gulf of Thailand. In: Proceedings of the 4th SEASTAR2000 Workshop. Pp. 15-19.Graduate School of Informatics, Kyoto University. http://hdl.handle. net/2433/44123. Accessed 10 June 2014.
Kittiwattanawong, K. & S. Manansap 2009. Tagging and satellite telemetry study in Thailand. In: Report on the Third Technical Consultation on Research for Stock Enhancement of Sea Turtles (Japanese Trust Fund IV Program) (eds. Kadir, S.A.S.A. & O. Abe).SEAFDEC- MFRDMD/RM/24:85-94.
Lau, M.M., S. Ruqaiyah, A. Devadasan, G.S. Duraisingham & R. Zullkifli. 2009. Satellite tracking of green turtles and hawksbill turtles in Peninsular Malaysia by WWF- Malaysia. In: Report on the Third Technical Consultation on Research for Stock Enhancement of Sea Turtles (Japanese Trust Fund IV Program) (eds. Kadir, S.A.S.A. & O. Abe). SEAFDEC-MFRDMD/RM/24:101-114.
Le Gall, J.Y. & G.R. Hughes. 1987. Migrations de la tortueverte Chelonia mydas dans l’Océan Indien Sud- Ouest observées à partir des marquagessur les sites de ponte Europa et Tromelin (1970–85). Amphibia-Reptilia 8: 277–282.
Limpus, C. J. 1997. Marine turtle populations of Southeast Asia and the western Pacific Region: Distribution and status. In: Proceedings of the Workshop on Marine Turtle Researchand Management in Indonesia (eds. Noor, Y. R., I.R. Lubis, R. Ounsted, S. Troeng, A. Abdullah). Pp. 37-72. Wetlands International, PHPA/Environment Australia, Bogor, Indonesia.
Limpus, C. J. 2007. A biological review of Australian marine turtles: 5. Flatback turtle, (Natator depressus) (Garman). State of Queensland, Environmental Protection Agency. ISBN 978-0-9803613-2-2.
Limpus, C.J. 2008a. A biological review of Australian marine turtles: 1. Loggerhead turtle, (Caretta caretta) (Linneaus). State of Queensland, Environmental Protection Agency. ISBN 978-0-9803613-2-2.
Limpus, C.J. 2008b. A biological review of Australian marine turtles: 2. Green turtle, (Chelonia mydas) (Linneaus). State of Queensland, Environmental Protection Agency. ISBN 978-0-9803613-2-2.
Limpus, C.J. 2009a. A biological review of Australian marine turtles: 3. Hawksbill turtle, (Eretomochelys imbricata) (Linneaus). State of Queensland, Environmental Protection Agency. ISBN 978-0-9803613-2-2.
Limpus, C.J. 2009b. A biological review of Australian marine turtles: 6. Leatherback turtle, (Dermochelys coriacea) (Vandelli). State of Queensland, Environmental Protection Agency. ISBN 978-0-9803613-2-2.
Limpus, C.J., J.D. Miller, C.J. Parmenter, D. Reimer, N. McLachlan, & R. Webb. 1992. Migration of green (Chelonia mydas) and loggerhead (Caretta caretta) turtles to and from eastern Australia rookeries. Wildlife Research 19: 347-358.
Lushci, P., J.R.E. Lutjeharms, P. Lambardi, R. Mencacci, G.R. Hughes & G.C. Hayes. 2006. A review of the migratory behaviour of sea turtles off southeastern Africa. South African Journal of Science 102: 51-58.
Mahardika G.N., I.A.C. Dewi, K.D. Nursanty, Y.L. Kote, D. Cahyani, A.S. Kendran, C.S. Nindhia et al. 2007. Mapping of the genetic stocks of green and hawksbill turtles in Derawan Islands, Berau, East Kalimantan. Project Report. Conservation International Indonesia– Animal Medical, Molecular Biology and Genetic Research Center Faculty of Veterinary Medicine Udayana University, Denpasar, Bali. Pp 1 – 40.
Miller J. 1989. An assessment of the conservation status of
marine turtles in the Kingdom of Saudi Arabia. Technical Report. MEPA Coastal and Marine Management Series 9: 1-209.
Minami, H., T. Nobetsu, K. Yokota, T. Hosono, H. Suganuma & S. Tanaka. 2009. Report on satellite telemetry activities from Japan (West Papua). In: Report on the Third Technical Consultation on Research for Stock Enhancement of Sea Turtles (Japanese Trust Fund IV Program) (eds. Kadir, S.A.S.A. & O. Abe)SEAFDEC-MFRDMD/RM/24:115-124.
Moritz, C. 1994. Defining evolutionary units for conservation. Trends in Ecology and Evolution 9: 373-375.
Moritz, C., D. Broderick, K. Dethmers, N. FitzSimmons & C. Limpus. 2002. Population genetics of southeast Asian and western Pacific green turtles, Chelonia mydas. Final Report to UNEP/CMS.
Mortimer, J.A. & D. Broderick. 1999. Population genetic structure and developmental migrations of sea turtles in the Chagos Archipelago and adjacent regions inferred from mtDNA sequence variation. In: Ecology of the Chagos Archipelago (eds. Sheppard, C.R.C. & M.R.D. Seaward). Linnean Society Occasional Publications 2: 185-194. Westbury Publishing.
Nel, R. 2012. Assessment of the conservation status of the leatherback turtle in the Indian Ocean and South-East Asia. IOSEA Marine Turtle MoU Secretariat, Bangkok.
Nishizawa, H., O. Abe, J. Okuyama, M. Kobayashi, & N. Arai 2011. Population genetic structure and implications for natal philopatry of nesting green turtles Chelonia mydas in the Yaeyama Islands, Japan. Endangered Species Research 14: 141-148.
Nishizawa, H., Y. Naito, H. Suganuma, O. Abe, J. Okuyama, K. Hirate, S. Tanaka et al. 2013. Composition of green turtle feeding aggregations along the Japanese archipelago: Implications for changes in composition with current flow. Marine Biology 160: 2671-2685.
Norman, J.A., C. Moritz & C.J. Limpus. 1994. Mitochondrial DNA control region polymorphisms: Genetic markers for ecological studies of marine turtles. Molecular Ecology 3: 363-373.
Okayama, T., R. Díaz-Fernández, Y. Baba, M. Halim, O. Abe, N. Azeno & H. Koike. 1999. Genetic diversity of the hawksbill turtle in the Indo-Pacific and Caribbean Regions. Chelonian Conservation and Biology 3: 312-317.
Pacioni, C., S. Trocini, M.R. Heithaus, D. Burkholder, J. Thomson, K. Warren & M. Krützen. 2012. Preliminary assessment of the genetic profile of the Western Australian loggerhead turtle population using mitochondrial DNA. In: Western Australian Sea Turtle Symposium 28-29th August 2012. (comps. Prince, R.I.T., S. Whiting, H. Raudino,
Indian Ocean Turtle Newsletter No. 20
A. Vitenbergs & K. Pendoley). P.19. Western Australia Department of Parks and Wildlife, Perth, Australia.
Palsbøll, P.J., M Bérubé & F.W.Allendorf. 2007. Identification of management units using population genetic data. Trends in Ecology and Evolution 22: 11-15.
Pittard, S.D. 2010. Genetic population structure of the flatback turtle (Natator depressus): A nuclear and mitochondrial DNA analysis. Honour’s Thesis, University of Canberra, Canberra, Australia.
Prince, R.I.T. 2004. Stranding of small leatherback turtle in Western Australia. Marine Turtle Newsletter 104:3-5.
Read, T.C., L. Wantiez, J.M. Werry, R. Farman, G. Petro & C.J. Limpus. 2014. Migrations of green turtles (Chelonia mydas) between nesting and foraging grounds across the Coral Sea. PLoS ONE 9(6): e100083. doi:10.1371/journal. pone.0100083.
Read, T., N.N. FitzSimmons, L. Wantiez, O. Chateau, J. Werry, R. Farman & C.J. Limpus. In Press. Genetic structure of the resident C. mydas population of the Grand Lagon Sud, New Caledonia. In: Proceedings of the 34thAnnual Sea Turtle Symposium on Sea Turtle Biology and Conservation. NOAA Technical Memorandum NOAA NMFS-SEFSC-XX:XX-XX.
Roden, S.E, P.A. Morin, A. Frey, G.H. Balazs, P. Zarate, I-J. Cheng & P.H. Dutton. 2013. Green turtles population structure in the Pacific: new insights from single nucleotide polymorphisms and microsatellites. Endangered Species Research 20: 227-234.
Ross, J.P. 1984. Biology of the green turtle Chelonia mydas on an Arabian feeding ground. Herpetologica 40: 1-14.
Sagun, V.G. 2003. Marine turtles with foreign tags recaptured in the Philippines from 1993 to 2002. In: Proceedings of the 4th SEASTAR2000 Workshop. Pp. 47-50. Graduate School of Informatics, Kyoto University. http://hdl.handle.net/2433/44131. Accessed 12 June 2014.
Sagun, V.G. 2004. Postnesting movements of green turtles tagged in the Turtle Islands Tawi-Tawi, Philippines. Marine Turtle Newsletter 104: 5-7.
Shamblin, B.M., A.B. Bolten, F.A. Abreu-Grobois, K.A. Bjorndal, L. Cardona, C. Carreras, M. Clusa et al. 2014. Geographic patterns of genetic variation in a broadly distributed marine vertebrate: New insights into loggerhead turtle stock structure from expanded mitochondrial DNA sequences. PLoS ONE 9: e85956. doi:10.1371/journal. pone.0085956.
Shanker, K., J. Ramadevi, B.C. Choudhury, L. Singh & R.K. Aggarwal. 2004. Phylogeography of olive ridley turtles (Lepidochelys olivacea) on the east coast of India:
Implications for conservation theory. Molecular Ecology 13: 1899-1909.
Shanker, K., B.C. Choudhury & R.K. Aggarwal. 2011. Conservation genetics of marine turtles on the mainland coast of India and offshore islands. Final Project Report. Wildlife Institute of India, Dehradun and Centre for Cellular and Molecular Biology, Hyderabad.
Tabib M., H. Zolgharnein, M. Mohammadi, M.A. Salari- Aliabadi, A. Qasemi, S. Roshani, H. Rajabi-Maham et al. 2011. mtDNA variation of the critically endangered hawksbill turtle (Eretmochelys imbricata) nesting on Iranian islands of the Persian Gulf. Genetics and Molecular Research 10: 1499-1503.
Tabib, M., F. Frootan & M. Askari Hesni. 2014. Genetic diversity and phylogeography of hawksbill turtle in the Persian Gulf. Journal of Biodiversity and Environmental Sciences 4: 51-57.
Van de Merwe, J.P., K. Ibrahim,S.Y. Lee & J.M. Whittier. 2009. Habitat use by green turtles (Chelonia mydas) nesting in Peninsular Malaysia: local and regional conservation implications. Wildlife Research 36: 637-645.
Velez-Zuazo, X., G.N. Mahardika, F. Ballamu, G. Gearheart, C.S. Kendran, A. Suartini & D. Cahyani. 2006. Genetic composition of the nesting aggregation of green turtles in the Archipelago of Raja Ampat, Indonesia. Project Report. Conservation International Indonesia – Animal Medical, Molecular Biology and Genetic Research Center Faculty of Veterinary Medicine Udayana University, Denpasar, Bali.
Wallace, B.P., A.D. DiMatteo, B.J. Hurley, E.M. Finkbeiner, A.B. Bolten, M.Y. Chaloupka, B.J. Hutchinson et al. 2010. Regional management units for marine turtles: A novel framework for prioritizing conservation and research across multiple scales. PLoS ONE 5: e15465. doi:10.1371/ journal.pone.0015465.
Wallace B.P. , A.D. DiMatteo, A.B. Bolten, M.Y. Chaloupka, B.J. Hutchinson, F.A. Abreu-Grobois, J.A.Mortimer et al. 2011. Global conservation priorities for marine turtles. PLos ONE 6: e24510. doi:10.1371/journal.pone.0024510
Waples, R.S. & O. Gaggiotti. 2006. What is a population? An empirical evaluation of some genetic methods for identifying the number of gene pools and their degree of connectivity. Molecular Ecology 15: 1419-1439.
Whiting, S.D., J.L. Long & M. Coyne. 2007. Migration routes and foraging behaviour of olive ridley turtles Lepidochelys olivacea in northern Australia. Endangered Species Research 3: 1-9.
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