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W., and R. L. Burke, editors. 1989. Crocodilian, tuatara, and turtle species of the world: a taxonomic and geographic reference. Association of Systematics Collections, Washington, D.C. 216 pp.","conceptName":"<i>Dermochelys coriacea</i>","taxonomicComments":"Two previously described subspecies, <i>D. c. coriacea</i> (Atlantic Ocean) and <i>D. c. schlegelii</i> (Pacific and Indian oceans), are poorly differentiated and are not recognized (Pritchard 1980).<br/><br/>Crother et al. (2008) has returned to the use of \"sea turtles\" (rather than \"seaturtles\") as part of the standard English name for marine turtles. The combined name has not been used recently in the literature.","roundedGRank":"G2","conservationStatusFactorsEditionDate":"2025-10-14","conservationStatusFactorsEditionAuthors":"Jackson, D. R., and G. Hammerson (2011); rev. R. L. 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species has a nearly global distribution. However, the population suffered historical declines well over 50% and continues to decline throughout much of the range with the only stable populations being in the Atlantic Ocean. It is threatened by nesting habitat loss and degradation, human consumption, by-catch and entanglement in commercial fishing gear, and plastic pollution.","grank":"G2G3","rankInfo":{"elementGlobalId":103708,"aooPercentGood":null,"enviromentalSpecificity":null,"intrinsicVulnerability":{"id":1,"intrinsicVulnerabilityDescEn":"Highly vulnerable","intrinsicVulnerabilityDescEs":"Altamente vulnerable","intrinsicVulnerabilityDescFr":"Très vulnérable"},"longTermTrend":{"id":12,"longTermTrendDescEn":"Decline of 50-90%","longTermTrendDescEs":"Disminución de 50 a 90%.","longTermTrendDescFr":"Diminution de 50 à 90 %"},"numberEos":{"id":11,"numberEosDescEn":"21 - 300","numberEosDescEs":"De 21 a 300","numberEosDescFr":"De 21 à 300"},"numberGoodEos":{"id":13,"numberGoodEosDescEn":"Few to some (4-40)","numberGoodEosDescEs":"Pocos a algunos (4-40)","numberGoodEosDescFr":"De peu à quelques-uns (de 4 à 40)"},"numberProtEos":{"id":7,"numberProtEosDescEn":"Few to several (1-12) occurrences appropriately protected and managed","numberProtEosDescEs":"Gradualmente hasta unos pocos casos (1 a 12) adecuadamente protegidos y controlados","numberProtEosDescFr":"De peu à quelques occurrences (de 1 à 12) protégées et contrôlées convenablement"},"popSize":{"id":31,"popSizeDescEn":"10,000 - 100,000 individuals","popSizeDescEs":"De 10.000 a 100.000 individuos","popSizeDescFr":"De 10 000 à 100 000 individus"},"rangeExtent":{"id":35,"rangeExtentDescEn":">2,500,000 square km (greater than 1,000,000 square miles)","rangeExtentDescEs":">2.500.000 kilómetros cuadrados (más ","rangeExtentDescFr":">2 500 000 km carrés (plus de 1 000 000 miles carrés)"},"shortTermTrend":{"id":31,"shortTermTrendDescEn":"Decline of 30-50%","shortTermTrendDescEs":"Disminución del 30 al 50%.","shortTermTrendDescFr":"Diminution de 30 à 50 %"},"threatImpactAssigned":{"id":5,"threatImpactAssignedDescEn":"High","threatImpactAssignedDescEs":"Alto","threatImpactAssignedDescFr":"Élevé"},"rangeExtentComments":"This circumglobal species generally forages in temperate waters and nests in tropical and subtropical latitudes on beaches of the Atlantic, Indian, and Pacific Oceans. Leatherbacks appear to spend the first portion of their lives entirely in tropical waters; those less than 100 cm in carapace length occur only in waters warmer than 26°C, whereas adults may venture to high latitude waters in summer (e.g., see Goff and Lien 1988, Eckert 2002) and occur occasionally in inshore waters.<br/><br/>Significant nesting areas include Malaysia (at least formerly), Pacific coast of Mexico and Central America, and Atlantic shore of northern South America. Largest population worldwide is in the western Atlantic (Spotila et al. 1996). In the Western Hemisphere, nesting also occurs in Florida (very rarely north to Georgia), along the shores of the Gulf of Mexico, in the West Indies, and along the Atlantic shore of Central America and the Pacific shore of northern South America. In the western Caribbean, nesting is frequent from northern Costa Rica to Colombia and in eastern French Guiana and western Surinam. Some nesting occurs along the central Brazilian coast; important colonies are in northwestern Guyana and in Trinidad. In the Antilles, most nesting occurs in the Dominican Republic and on islands close to Puerto Rico, including Culebra and St. Croix (the largest, best-studied population in U.S. waters).<br/><br/>A general aggregation of leatherbacks is known to occur in the Pacific north of the Hawaiian Islands year-round, and in the Atlantic seasonal concentrations occur during the summer and fall months in the northeastern United States and Canada in areas such as Cape Cod Bay, the Gulf of Maine, the Scotian Shelf, and Cape Breton.","areaOfOccupancy":null,"areaOfOccupancyComments":null,"numberEosComments":"There are at least 400 nesting sites (NMFS and USFWS 2013), though some would likely be considered the same occurrence.","popSizeComments":"Pritchard (1982) estimated 115,000 breeding females worldwide, though his estimates may have been too high, especially for Mexico. Estimated world population in the early 1990s was reported as 136,000 breeding females by Pritchard (1992). In contrast, Spotila et al. (1996) estimated the worldwide population of nesting females at 26,200-42,000, with the majority of animals occurring in the Atlantic Ocean and Caribbean Sea where the population was estimated at 27,608. An estimated 100-900 leatherbacks occur in summer in waters off the northeastern U.S. (Shoop and Kenney 1992). See Cook (1981) for information on status in Canada.<br/><br/>Spotila et al. (2000) estimated total adult (breeding) population at 1,690 females in the eastern Pacific (down from an estimated 4,600-6,500 in 1996) and concluded leatherbacks are on the verge of extinction in the Pacific. Another estimate suggested a total of 2,300 adult females in the entire Pacific (Crowder 2000).<br/><br/>In Florida, between 1988 and 1992, annual reported leatherback nests varied between 98 and 188 (USFWS 1998). In the 1980s and early 1990s, about 18-55 females nested each year on St. Croix in the U.S. Virgin Islands (Boulon et al. 1996); increased to 100+ in 1997. In 1997, more than 80 females nested at Culebra Island, Puerto Rico.<br/><br/>Nest counts at the largest nesting colony in Mexico reported less than 250 in 1998-1999 (Eckert unpubl. results in Spotila et al. 2000). Spotila et al. (2000) predicted that without protection the population breeding at Playa Grande, Costa Rica (once the 4th largest nesting colony in the world), would be reduced to around 50 nesting females by 2003-2004.<br/><br/>In the mid-1990s, few beaches had more than a few hundred nesting females (Spotila et al. 1996). Only four nesting areas presently support more than 1,000 breeding females: the Pacific coast of Mexico probably fewer than 5,000 though formerly many more; Pacific coast of French Guiana, 4,500-6,500; peninsular Malaysia, 1,000-2,000; and the Kepala Burung region of Indonesia (UNEP 2003).","viabilityComments":"Seven nesting sites have been documented with increasing trends and three more with stable trends (NMFS and USFWS 2013). Several other nesting sites with large population sizes and may have good viability (NMFS and USFWS 2013).","threatImpactComments":"Major threats include egg collecting and mortality associated with bycatch in longline, trawl, and gillnet fisheries throughout the range (Spotila et al. 2000, Ferraroli et al. 2004, Lewison et al. 2004). Other concerns include harvest of adult females at nest beaches for meat and oil, nesting habitat loss, pollution, and adult ingestion of floating plastics and trash (Lewison et al. 2004, Barragan et al. 2022).<br/><br/>Egg harvesting: Most nest beaches are now protected in Mexico and in other parts of range, but egg exploitation continues. A long history of egg collection contributed to population declines in Malaysia (Chan and Liew 1996). In the 1980s, cash value of leatherback eggs was still so high that the Trengganu Fisheries Department could only afford to buy back a small percentage of harvested eggs for incubation and release (Pritchard 1982).<br/><br/>Fisheries bycatch: Leatherback are especially threatened by longline swordfish and tuna fisheries of the United States, Europe, Asia, and South America, shrimp trawl fisheries, gillnet fisheries, and pot fisheries throughout the world. Even with the use of larger Turtle Excluder Devices (TEDs) developed to exclude leatherbacks, the U.S. offshore commercial shrimp fishery captures an estimated 640 each year (NOAA/NMFS 2005). Eckert and Sarti (1997) reported that \"mortality associated with the swordfish gillnet fisheries in Peru and Chile represents the single largest source of mortality for East Pacific leatherbacks\". Gillnet fisheries in these countries may kill an estimated 2,000 leatherbacks annually (this estimate does not include animals taken in the longline fishery; Eckert and Sarti 1997). During 2000, an estimated 20,000 leatherbacks were caught and 1,000-3,200 killed as bycatch in Pacific longline fisheries (Lewison et al. 2004). The U.S. contribution to total pelagic longline bycatch is only around 2% of the global take, so most of the threat of capture exists outside the United States(Lewison et al. 2004). From 1978-1981, 126 turtles were reported captured in the Japanese tuna longline fishery in the Atlantic/Gulf of Mexico, of which around 25% were leatherbacks (Spotila et al. 1996). Hundreds of turtles are entangled in lines associated with traps/pots for commercial fishing (Dodge et al. 2023).<br/><br/>Other threats: Adults historically were taken for meat and oil on nest beaches, and poaching still occurs in some locations. Erosion, development, and disturbance of nest beaches threatens nest success and reduces available nesting habitat (Pritchard 1982, NOAA/NMFS 2005). Where space is limited, females have been observed constructing nests on occupied sites and destroying eggs already present. Nesting beaches throughout their range are subject to human-related impacts including: coastal development, beach armoring, dredging, and beachfront lighting. Ingestion of floating plastic trash mistaken for jellyfish is often fatal to leatherbacks; vessel dumping of discarded fishing gear and petroleum products is also of concern (Bolten and Bjorndal 1992, NOAA/NMFS 2005).","shortTermTrendComments":"Of 20 nesting sites with available data, 7 were increasing, 3 were stable, and 10 were decreasing (NMFS and USFWS 2013). None of the sites in the Pacific or Indian oceans were increasing; all sites with increasing trends were in the Atlantic (NMFS and USFWS 2013). However, the Atlantic population is considered declining (Barragan et al. 2022). At the foraging grounds off the Pacific Coast of the U.S., this species declined by 5.6% annually from 1990-2017 resulting in an estimated 80% overall decline (Benson et al. 2020). From 2002-2022, the populations at Bocas del Toro region of Panamá showed an overall declining trend (Gutiérrez Parejo et al. 2025). The number of nests remained stable from 1994-2012 at Pacuare Nature Reserve on the Pacific coast of Costa Rica (Rivas et al. 2015).","longTermTrendComments":"Spotila et al. (1996) summarized information indicating that a major decline has occurred in recent decades; this was questioned by Pritchard (1996). Declines in the number of nesting females have been documented in Malaysia, India, Thailand, and the West Indies (USFWS 1998, NMFS and USFWS 2013).<br/><br/>The eastern Pacific leatherback population, in particular, appears to have declined dramatically. In the early 1980s the total Pacific population estimate was 87,000-91,000 breeding females, with 12,000 occurring in the East Pacific outside of Mexico (Pritchard 1982, Spotila et al. 1996). In 2000, Spotila et al. (2000) estimated only 1,690 breeding females in the eastern Pacific. The population nesting along Mexico's Pacific coast, which once supported as much as half of all global nesting, experienced a drastic decline in the 1980s and 1990s, with fewer than 1,000 females believed to have nested there during the 1995-1996 season; a decline of 22-55% annually over 12 years (Sarti et al. 1996). On a beach on the Pacific coast of Costa Rica, the number of nesting females fell from 1,367 in 1988/1989 to 231 in 1999/2000, a decline of almost 85% in 11 years (Reina et al. 2002). The decline reflects excessive adult mortality likely related to fishing industry practices (Spotila et al. 2000). A major population in Rantau Abang, Malaysia, declined from over 10,000 nests per year in 1956 to 3,100 in 1968 to fewer than 100 in the early to mid-1990s (Chan and Liew 1996).<br/><br/>The largest known nesting aggregation of leatherbacks in the western North Atlantic occurs in French Guiana and has been declining by about 15% annually since 1987 (NMFS Southeast Fisheries Science Center 2001). Current trend of populations under U.S. jurisdiction is uncertain (USFWS 1998). Small nesting populations in Florida and on St. Croix, U.S. Virgin Islands, and Culebra Island, Puerto Rico, have increased significantly since early 1980s, but magnitude of nesting in these areas is much less than at other breeding sites (NMFS Southeast Fisheries Science Center 2001).","inventoryNeeds":"More long-term monitoring programs needed in the Indian and Pacific oceans.","numberProtEosComments":"The Inter-American Convention for the Protection and Conservation of Sea Turtles (IAC) is the only treaty devoted exclusively to sea turtles and aims to \"promote the protection, conservation and recovery of sea turtle populations and of the habitats on which they depend, based on the best available scientific evidence, taking into account the environmental, socioeconomic and cultural characteristics of the Parties.\" This treaty involves 21 nations, including the United States, in preserving sea turtles as an internationally shared resource (seaturtle.org 2003, C. Ryder, pers. comm.).<br/><br/>Critical Habitat has been designated at St. Croix, Virgin Islands; Santa Rosa N.P., Costa Rica; and sites in Mexico.<br/><br/>NMFS (Federal Register, 12 May 1995) established a leatherback conservation zone extending from Cape Canaveral to the Virginia-North Carolina border and including all inshore and offshore waters; this zone is subject to shrimping closures when high abundances of leatherbacks are documented. For example, on 20 December 2001, NOAA Fisheries issued a temporary rule that required shrimp trawlers operating in Atlantic waters from the shoreline out to 10 nautical miles between 28 degrees north latitude, approximately Melbourne, Florida and the Florida/ Georgia border, to use Turtle Excluder Devices (TEDs) with escape openings modified to exclude leatherback turtles. This emergency rule, effective through 14 January 2002, was based on a number of factors including the presence of an extraordinarily high number of leatherbacks stranded along northeast Florida beaches in November and early December. According to state authorities, 15 dead leatherbacks washed ashore from St. Johns through Brevard counties in shrimp zones 28 and 29 between November 4 and December 10, 2001 (NMFS 2000). Turtle exclusion device (TED) programs have been initiated in several other countries as well. Larger TEDs that are more effective in excluding larger hard-shelled and leatherback turtles are now required in certain areas during specified times. Use of TEDs with openings large enough to accommodate leatherbacks is required of U.S. shrimp trawlers in the Atlantic and Gulf of Mexico.<br/><br/>In 1989, a law was passed (Section 609 of U.S. Public Law 101-162) prohibiting U.S. importation of shrimp harvested in ways that are harmful to sea turtles; only nations certified by the Department of State as having a sea turtle protection program similar to that in the United States (i.e., requiring and enforcing TED use) may avoid this trade embargo. Time length of individual shrimp trawls is also limited to reduce drowning risk to trapped sea turtles, and fisheries observers are required on a certain percentage of U.S. vessels fishing the North Pacific, Atlantic, and Gulf of Mexico.<br/><br/>Nest beaches are protected in most parts of the species' range, but outside of U.S. jurisdiction law enforcement is often insufficient (Showalter 2003).","protectionNeeds":"Protection needs include the following: protect all existing occurrences (increase survival of eggs and hatchlings); reduce adult mortality, such as by reducing incidental catch (mandatory use of TEDs, elimination of drift nets); restrict dumping of plastics and other debris and pollutants.<br/><br/>See also recovery plans and Spotila et al. (1996).","otherConsiderations":"Individuals may move hundreds to thousands of kilometers between nesting beaches and distant marine waters; this increases vulnerability to incidental take.","intrinsicVulnerabilityComments":"Female age at maturity is not explicitly known but could be 20 years or more (NMFS and USFWS 2013). Nesting occurs on the same beaches during the same seasonal period each year, leaving the species vulnerable to poaching.","enviromentalSpecificityComments":null},"animalCharacteristics":{"elementGlobalId":103708,"majorHabitat":{"id":1,"majorHabitatDescEn":"Marine","majorHabitatDescEs":"Marino","majorHabitatDescFr":"Marine"},"nonMigrant":false,"localMigrant":false,"longDistanceMigrant":true,"mobilityMigrationComments":"Moves hundreds or thousands of kilometers between nesting beaches and distant marine waters; transequatorial migrations have been documented. Pattern of epibiont colonization in Caribbean suggests that gravid turtles do not arrive from temperate latitudes until just prior to nesting, and that they go directly to a preferred nesting beach; nesters apparently arrive asynchronously (Eckert and Eckert 1988). Individual females may nest on multiple islands within a region; a female that nested on St. Croix, Virgin Islands, during the next 18 days, nested also on Isla Vieques and Isla Culebra (Keinath and Musick 1993); see also Boulon et al. (1996). Caribbean nesters apparently move north along Atlantic coast after nesting (appear at least as far north as the northeastern U.S. in late summer; Boulon et al. 1988). A leatherback tagged in Chesapeake Bay in late May 1985 was captured off southern Cuba in late July 1986 (Keinath and Musick 1990). Leatherbacks from nesting areas in Suriname and Costa Rica (Caribbean coast) were found in summer off Nova Scotia (James 2004).<br><br>Morreale et al. (1996) documented a migration corridor extending from the Pacific coast of Costa Rica through the vicinity of the Galapagos Islands. <br><br>A nesting female tagged in Suriname was captured off Ghana, West Africa, less than 1 year later (Eckert 1992).","foodHabitsComments":"Principal food is jellyfish, though other invertebrates, fishes, and seaweed sometimes are eaten. Pelagic foraging may focus on jellyfish in the deep scattering layer (Eckert 1992).","animalPhenologyComments":null,"colonialBreeder":true,"length":178,"width":null,"weight":544000,"animalPhenologies":[],"animalFoodHabits":[{"animalCagFoodHabitsId":104817,"foodHabits":{"id":3,"foodHabitsDescEn":"Invertivore","foodHabitsDescEs":"Invertívoro","foodHabitsDescFr":"Invertivore","displayOrder":3},"adult":true,"immature":true}]},"occurrenceDelineations":[{"eoSpecsDetailId":1189,"locationUseClass":{"id":7,"locationUseClassDescEn":"Hibernaculum","locationUseClassDescEs":"Hibernáculo","locationUseClassDescFr":"Gîte d’hibernation","displayOrder":8},"eoSpecGroupName":"Sea Turtles (Cheloniidae and Dermochelyidae)","subtypes":null,"inferredExtentDistance":null,"inferredExtentNotes":null,"minimumEoCriteria":"Reliable observation of multiple dormant individuals. Multiple years of information should be used to reliably identify significant, persistent occurrences.","mappingGuidance":null,"separationBarriers":null,"separationDistanceUnsuitableHabitatat":10.0,"separationDistanceSuitableHabitatat":10.0,"altSeparationProcedure":null,"separationJustification":"Separation distance refers to known concentrations of dormant individuals.  In most cases, occurrences should not be extensive areas such as the Atlantic coast of Florida but rather portions of such areas that stand out as strongly meeting the occurrence criteria.  <br><br>Analyses of mitochondrial DNA variation have increased our understanding of the phylogenetic relationships among certain populations of sea turtles and have allowed the recognition of some evolutionarily distinctive units. However, available information on genetics, dispersion, and movement patterns of most sea turtle populations generally is insufficient to determine biologically meaningful separation distances for the different kinds of occurrences covered by the specifications. The separation distances used here do not attempt to identify biologically distinct populations but rather are arbitrary values that attempt to identify relatively distinct geographic areas that have frequent or concentrated activity and that are of practical size for conservation use. Additionally, these specifications assume that it is best to have uniform occurrence standards for all sea turtle species, placing greater emphasis on the general similarity of their life history patterns than on specific biological differences among species.","versionDate":"2004-10-20","versionAuthor":"Hammerson, G.","versionNotes":null,"lastModified":"2020-04-30T02:04:22.159951Z"},{"eoSpecsDetailId":1191,"locationUseClass":{"id":15,"locationUseClassDescEn":"Adult foraging area","locationUseClassDescEs":"Zona de alimentación de adultos","locationUseClassDescFr":"Aire d’alimentation adulte","displayOrder":15},"eoSpecGroupName":"Sea Turtles (Cheloniidae and Dermochelyidae)","subtypes":null,"inferredExtentDistance":null,"inferredExtentNotes":null,"minimumEoCriteria":"Reliable observation of multiple adults in an area that supports productive populations of appropriate food organisms. Multiple years of information should be used to reliably identify significant, persistent occurrences.","mappingGuidance":null,"separationBarriers":"None.","separationDistanceUnsuitableHabitatat":10.0,"separationDistanceSuitableHabitatat":10.0,"altSeparationProcedure":null,"separationJustification":"Separation distance refers to known areas of concentrated foraging activity. In most cases, occurrences should not be extensive areas such as the entirety of Long Island Sound or Chesapeake Bay but rather portions of such areas that stand out as strongly meeting the occurrence criteria.  <br><br>Analyses of mitochondrial DNA variation have increased our understanding of the phylogenetic relationships among certain populations of sea turtles and have allowed the recognition of some evolutionarily distinctive units. However, available information on genetics, dispersion, and movement patterns of most sea turtle populations generally is insufficient to determine biologically meaningful separation distances for the different kinds of occurrences covered by the specifications. The separation distances used here do not attempt to identify biologically distinct populations but rather are arbitrary values that attempt to identify relatively distinct geographic areas that have frequent or concentrated activity and that are of practical size for conservation use. Additionally, these specifications assume that it is best to have uniform occurrence standards for all sea turtle species, placing greater emphasis on the general similarity of their life history patterns than on specific biological differences among species.<br><br>Foraging home range sizes of individual hawksbill turtles in the West Indies were 1.96-49.5 sq km and were positively correlated with average water depth (Horrocks et al. 2001). <br>","versionDate":"2004-10-20","versionAuthor":"Hammerson, G.","versionNotes":null,"lastModified":"2020-04-30T02:04:22.159951Z"},{"eoSpecsDetailId":1192,"locationUseClass":{"id":17,"locationUseClassDescEn":"Juvenile foraging area","locationUseClassDescEs":"Zona de alimentación de los jóvenes","locationUseClassDescFr":"Aire d’alimentation juvénile","displayOrder":16},"eoSpecGroupName":"Sea Turtles (Cheloniidae and Dermochelyidae)","subtypes":null,"inferredExtentDistance":null,"inferredExtentNotes":null,"minimumEoCriteria":"Reliable observation of multiple juveniles in an area that supports productive populations of appropriate food organisms. Multiple years of information should be used to reliably identify significant, persistent occurrences.","mappingGuidance":null,"separationBarriers":null,"separationDistanceUnsuitableHabitatat":10.0,"separationDistanceSuitableHabitatat":10.0,"altSeparationProcedure":null,"separationJustification":"Separation distance refers to known areas of concentrated foraging activity. In most cases, occurrences should not be extensive areas such as the entirety of Long Island Sound or Chesapeake Bay but rather portions of such areas that stand out as strongly meeting the occurrence criteria.  <br><br>Analyses of mitochondrial DNA variation have increased our understanding of the phylogenetic relationships among certain populations of sea turtles and have allowed the recognition of some evolutionarily distinctive units. However, available information on genetics, dispersion, and movement patterns of most sea turtle populations generally is insufficient to determine biologically meaningful separation distances for the different kinds of occurrences covered by the specifications. The separation distances used here do not attempt to identify biologically distinct populations but rather are arbitrary values that attempt to identify relatively distinct geographic areas that have frequent or concentrated activity and that are of practical size for conservation use. Additionally, these specifications assume that it is best to have uniform occurrence standards for all sea turtle species, placing greater emphasis on the general similarity of their life history patterns than on specific biological differences among species.<br>","versionDate":"2004-10-20","versionAuthor":"Hammerson, G.","versionNotes":null,"lastModified":"2020-04-30T02:04:22.159951Z"},{"eoSpecsDetailId":1190,"locationUseClass":{"id":16,"locationUseClassDescEn":"Nesting area","locationUseClassDescEs":"Zona de anidación","locationUseClassDescFr":"Aire de nidification","displayOrder":17},"eoSpecGroupName":"Sea Turtles (Cheloniidae and Dermochelyidae)","subtypes":null,"inferredExtentDistance":null,"inferredExtentNotes":null,"minimumEoCriteria":"Occurrences are based on evidence of historical presence, or current and likely recurring presence, at a given location. Such evidence minimally includes collection or reliable observation and documentation of one or more nesting individuals or nests with eggs.","mappingGuidance":null,"separationBarriers":"None.","separationDistanceUnsuitableHabitatat":10.0,"separationDistanceSuitableHabitatat":10.0,"altSeparationProcedure":null,"separationJustification":"Analyses of mitochondrial DNA variation have increased our understanding of the phylogenetic relationships among certain populations of sea turtles and have allowed the recognition of some evolutionarily distinctive units. However, available information on genetics, dispersion, and movement patterns of most sea turtle populations generally is insufficient to determine biologically meaningful separation distances for the different kinds of occurrences covered by the specifications. The separation distances used here do not attempt to identify biologically distinct populations but rather are arbitrary values that attempt to identify relatively distinct geographic areas that have frequent or concentrated activity and that are of practical size for conservation use. Additionally, these specifications assume that it is best to have uniform occurrence standards for all sea turtle species, placing greater emphasis on the general similarity of their life history patterns than on specific biological differences among species.<br><br>Nesting populations on separate islands or mainland areas within the separation distance should be treated as parts of the same occurrence. However, each distinct nesting location can be treated as a distinct sub-occurrence (sub-EO) or source feature for which specific data can be recorded.","versionDate":"2004-04-26","versionAuthor":"Hammerson, G.","versionNotes":null,"lastModified":"2020-04-30T02:04:22.159951Z"}],"plantCharacteristics":null,"elementManagement":{"elementGlobalId":103708,"eoManagementGroupName":null,"stewardshipOverview":null,"impacts":null,"restorationPotential":null,"siteConservationPlansConsidered":null,"managementMethods":"Basic needs are to: monitor occurrences; enforce protective regulations; conduct educational programs regarding sea turtles, particularly in Mexico, South America, and Malaysia; enact beach lighting ordinances; keep traffic off beaches; remove nest predators (e.g., raccoons, canids, coatis) if needed. <br><br>Frazer (1992) emphasized the primary need for clean and productive marine and coastal environments; installation of turtle excluder devices in shrimp trawl nets and use of low pressure sodium lighting on beaches were suggested as appropriate sea turtle conservation technologies, whereas headstarting, captive breeding, and hatcheries were regarded as ineffective at best. <br><br>See NMFS (Federal Register, 19 December 1996, pp. 66933-66947) for recent amendments to regulations pertaining to the use of turtle excluder devices along the Gulf and Atlantic coasts of the southeastern U.S. <br><br>At Sandy Point National Wildlife Refuge, U.S. Virgin Islands, nest relocations and protection from poaching possibly have resulted in a doubling of the number of emerging hatchlings (Boulon et al. 1996). <br><br>See Chan (1989) for information on handling eggs and artificial incubation. <br><br>A recovery plan is available for marine turtles: see Marine Turtle Recovery Team (1984). For detailed information on management and recovery, see also the recovery plans for the St. Croix population (1981), U.S. Pacific populations (NMFS 1998), and South Florida population (USFWS 1998).","monitoringMethods":"See Mrosovsky and Benabib (1990) for an evaluation of methods for sexing hatchlings. See Eckert and Eckert (1989) for information on tagging. See McDonald and Dutton (1996) for information on the use of PIT tags and photoidentification as useful supplements to tagging.","managementProgramContacts":"Nest surveys and protection have occurred on two major U.S. nesting beaches, Sandy Point (St. Croix, U.S. Virgin Islands) and Isla Culebra, (Puerto Rico); as of 1990, establishment of beach and turtle protection was planned for Mexiquillo (Michoacan, Mexico). <br><br>See NMFS (1993) for recent shrimp trawling regulations for an area off the coast of North Carolina (allow tow-time limits as an interim alternative to the use of turtle excluder devices). NMFS (1994, Federal Register, 5 May 1994) established all inshore and offshore waters from Cape Canaveral, Florida, to the North Carolina-Virginia border as the leatherback conservation zone, subject to shrimp trawling closure unless trawlers use NMFS-approved turtle excluder devices; closures were to be instituted if high turtle abundance levels were documented. <br><br>Wider Carribbean Sea Turtle Conservation Network (WIDECAST) is a United Nations-sponsored program devoted to the recovery of endangered Caribbean sea turtles.","monitoringProgramContacts":null,"managementResearchPrograms":null,"managementResearchNeeds":"Determine sustainability of egg harvest. Information needed on ecology, demographics, and migratory movements. Determine nest site tenacity.","biologicalResearchNeeds":"Better information is needed on ecology, demographics, migratory movements, nest site tenacity, bycatch, survivorship rates, and the status of stocks throughout the range.","additionalTopics":null},"occurrenceViabilities":[{"eoRankSpecsDetailId":105179,"eoRankSpecsGroupName":null,"locationUseClass":{"id":1,"locationUseClassDescEn":"Not applicable","locationUseClassDescEs":"No se aplica","locationUseClassDescFr":"Sans objet","displayOrder":1},"excellentViability":null,"goodViability":null,"fairViability":null,"poorViability":null,"viabilityJustification":"Use the Generic Guidelines for the Application of Occurrence Ranks (2008).<br>The Key for Ranking Species Occurrences Using the Generic Approach provides a step-wise process for implementing this method.","versionDate":null,"versionAuthor":null,"versionNotes":null,"lastModified":"2020-05-14T02:24:46.477184Z"}],"references":[{"id":1158882,"citation":"Benson, S. R., K. A. Forney, J. E. Moore, E. L. LaCasella, J. T. Harvey, and J. V. Carretta. 2020. A long-term decline in the abundance of endangered leatherback turtles, <i>Dermochelys coriacea</i>, at a foraging ground in the California Current Ecosystem. Global Ecology and Conservation 24: e01371. doi: 10.1016/j.gecco.2020.e01371","shortCitationAuthor":"Benson et al.","shortCitationYear":2020,"referenceCode":"A20BEN02NAUS","lastModified":"2025-11-01T14:10:38.140751Z"},{"id":137154,"citation":"Bjorndal, K. A., editor. 1982. Biology and conservation of sea turtles. Smithsonian Institution Press, Washington, D.C. 583 pp.","shortCitationAuthor":"Bjorndal","shortCitationYear":1982,"referenceCode":"B82BJO01NAUS","lastModified":"2022-01-11T02:14:44.338776Z"},{"id":622978,"citation":"Bolten, A.B., and K.A. Bjorndal. 1992. Effect of marine debris on juvenile, pelagic sea turtles: interim project report to the National Marine Fisheries Service Marine Entanglement Research Program. 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