{"elementGlobalId":105239,"circumscripConfidence":{"id":1,"circumscripConfidenceDescEn":"1 - Strong","circumscripConfidenceDescEs":"1 - Fuerte","circumscripConfidenceDescFr":"1 – Forte"},"classificationLevel":{"id":7,"classificationLevelNameEn":"Species","classificationLevelNameEs":"Especies","classificationLevelNameFr":"Espèce"},"classificationStatus":{"id":1,"classificationStatusDescEn":"Standard","classificationStatusDescEs":"Estándar","classificationStatusDescFr":"Standard"},"iucn":{"id":5,"iucnDescEn":"Vulnerable","iucnDescEs":"Vulnerable","iucnDescFr":"Vulnérable","iucnCode":"VU"},"nameCategory":{"id":1,"nameCategoryDescEn":"Vertebrate Animal","nameCategoryDescEs":"Animal vertebrado","nameCategoryDescFr":"Animal vertébré","nameTypeCd":"A","nameTypeDesc":"Zoological"},"rankMethodUsed":{"id":7,"rankMethodUsedDescEn":" Rank calculation - Biotics v2","rankMethodUsedDescEs":null,"rankMethodUsedDescFr":null,"rankMethodUsedExternalDescEn":"Ranked by calculator","rankMethodUsedExternalDescEs":null,"rankMethodUsedExternalDescFr":null},"formattedScientificName":"<i>Caretta caretta</i>","scientificName":"Caretta caretta","scientificNameAuthor":"(Linnaeus, 1758)","primaryCommonName":"Loggerhead Sea Turtle","relatedItisNames":"<i>Caretta caretta</i> (Linnaeus, 1758) (TSN 173830)","uniqueId":"ELEMENT_GLOBAL.2.105239","elcode":"ARAAA01010","conceptRefFullCitation":"King, F. 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>Caretta caretta</i>","taxonomicComments":"See Dodd (1988) for a discussion of taxonomy. Dodd (1988, 1990) recommended that subspecies not be recognized. Accordingly, Crother (2012, 2017) and Turtle Taxonomy Working Group (2012, 2021) recognized no subspecies.<br/><br/>MtDNA data from major nesting populations in the Atlantic, Indian, and Pacific oceans and the Mediterranean Sea indicate that most breeding colonies have diagnostic genetic characteristics, indicating strong natal homing by nesting females (Bowen et al. 1994). Two major matrilines were identified, and each occurred in both Atlantic-Mediterranean and Indian-Pacific samples. This was attributed to recent interoceanic gene flow, probably mediated by the ability of this turtle to utilize habitats around southern Africa.<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":"G3","conservationStatusFactorsEditionDate":"2024-09-29","conservationStatusFactorsEditionAuthors":"Jackson, D. R., and G. Hammerson; updated by S. 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distribution and not uncommon in warm oceans and seas; a few subpopulations declining significantly in recent years, but others stable or increasing. Many nesting sites are protected, though perhaps not adequately; subject to many threats that land conservation alone cannot solve.","grank":"G2G4","rankInfo":{"elementGlobalId":105239,"aooPercentGood":null,"enviromentalSpecificity":{"id":2,"enviromentalSpecificityDescEn":"Very narrow to narrow.","enviromentalSpecificityDescEs":"Muy estrecho a estrecho.","enviromentalSpecificityDescFr":"De très étroit à étroit."},"intrinsicVulnerability":{"id":1,"intrinsicVulnerabilityDescEn":"Highly vulnerable","intrinsicVulnerabilityDescEs":"Altamente vulnerable","intrinsicVulnerabilityDescFr":"Très vulnérable"},"longTermTrend":{"id":18,"longTermTrendDescEn":"Decline of 70-80%","longTermTrendDescEs":"Disminución del 70 al 80%.","longTermTrendDescFr":"Diminution de 70 à 80 %"},"numberEos":{"id":14,"numberEosDescEn":"81 to >300","numberEosDescEs":"De 81 a >300","numberEosDescFr":"De 81 à >300"},"numberGoodEos":null,"numberProtEos":{"id":14,"numberProtEosDescEn":"Many to very many (13 to >40) occurrences appropriately protected and managed","numberProtEosDescEs":"De varios a muchos casos (13 a >40) adecuadamente protegidos y controlados","numberProtEosDescFr":"De plusieurs à beaucoup d’occurrences (de 13 à >40) protégées et contrôlées convenablement"},"popSize":{"id":32,"popSizeDescEn":"10,000 - 1,000,000 individuals","popSizeDescEs":"De 10.000 a 1.000.000 de individuos","popSizeDescFr":"De 10 000 à 1 000 000 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":26,"shortTermTrendDescEn":"Decline of 30-70%","shortTermTrendDescEs":"Disminución del 30 al 70%.","shortTermTrendDescFr":"Diminution de 30 à 70 %"},"threatImpactAssigned":{"id":3,"threatImpactAssignedDescEn":"Very high - medium","threatImpactAssignedDescEs":"Muy alto - medio","threatImpactAssignedDescFr":"Moyen — très élevé"},"rangeExtentComments":"Warmer parts of Atlantic, Pacific, and Indian oceans, and Mediterranean and Caribbean seas (Bolten et al. 1992, Conant et al. 2009, COSEWIC 2010, Casale and Tucker 2017, Environment and Climate Change Canada 2020). Ranges into temperate zones in summer; rare or absent far from mainland shores. Major nesting areas are in warm temperate and subtropical areas in Oman, the southeastern U.S., Mexico, Australia, South Africa, the Mediterranean, and Japan (Dodd 1992). Conant et al. (2009) divided the global population into nine Distinct Population Segments (DPS), but subsequently the IUCN Red List assessment divides the North Indian Ocean DPS into two and thus defines 10 subpopulations. Separate Red List assessments are available for each IUCN subpopulation: North Pacific (Casale and Matsuzawa 2015), South Pacific (Limpus and Casale 2015), North West Indian Ocean (Casale 2015a), North East Indian Ocean (Casale 2015b), South East Indian Ocean (Casale et al. 2015), South West Indian Ocean (Nel and Casale 2015), North West Atlantic (Ceriani and Meylan 2017), North East Atlantic (Casale and Marco 2015), Mediterranean (Casale 2015c), and South West Atlantic (Casale and Marcovaldi 2015).<br/><br/>The world's largest nesting aggregation was on Masirah Island, Oman, although this has declined over the past few decades to 10,223-11,500 females (Willson et al. 2020).<br/><br/>The North West Atlantic subpopulation breeds mostly along the southeast coast of the United States (Shoop 1985, Dodd 1988, NMFS and USFWS 2011) and on the Yucatan Peninsula of Mexico (Ceriani and Meylan 2017), and its marine habitats extend throughout all the north and central Atlantic Ocean (northwest, northeast, central west and central east). This subpopulation hosts one of the two most significant nesting assemblages in the world, and over 85% of the nesting effort within the subpopulation is on beaches in peninsular Florida (NMFS and USFWS 2011). About 90% of the population nests in Brevard, Indian River, St. Lucie, Martin, Palm Beach, and Broward counties, Florida (CSTC 1990). Large numbers occur off primary nesting beaches in Florida during spring and summer (CSTC 1990). Nests regularly in small numbers in Virginia and sometimes north to New Jersey. In recent years a few have nested on barrier islands along the Texas coast. Chesapeake Bay is an important habitat for subadults in summer. Occurs in summer in waters off the northeastern U.S., mainly between Long Island and Cape Hatteras, usually in water less than 60 m deep (Shopp and Kenney 1992). See Seminoff et al. (2004) for information on occurrence in the Gulf of California. See Dodd (1988, 1990) for further details.","areaOfOccupancy":null,"areaOfOccupancyComments":null,"numberEosComments":"Represented by many occurrences throughout much of the range. Exact number not known, depends somewhat on partly subjective determination of EO-boundaries. There are at least two dozen major nesting areas worldwide (Dodd 1990).","popSizeComments":"Total population of mature (nesting) females is perhaps 36,000 to 67,000 (Casale and Tucker 2017), based on the number of nests. About 200,000 clutches are laid each year; a range of 3 to 5.5 clutches per adult female is used to estimate population size. However, the sex ratio of Loggerheads is not known, so extrapolating this number to the entire population is difficult (Ceriani and Meylan 2017).<br/><br/>The largest of the ten global subpopulations is the one inhabiting the North West Atlantic; at present about 83,717 nests are laid per year along the southeastern coast of the United States, which would translate to 15,200 to 27,900 nesting adult females (Casale and Tucker 2017). In Oman, what was formerly the world's largest concentration of nesting females has declined to 10,223-11,500 females in 2016 (Willson et al. 2020).<br/><br/>At least five different subpopulations have been identified in the western North Atlantic and Gulf of Mexico, with nesting abundance as follows (see NMFS 2002): (1) A Northern nesting subpopulation, occurring from North Carolina to northeast Florida at about 29 degrees N (about 7,500 nests in 1998); (2) a South Florida nesting subpopulation, occurring from 29 degrees N on the east coast to Sarasota on the west coast (approximately 83,400 nests in 1998); (3) a Florida Panhandle nesting subpopulation, occurring at Eglin Air Force Base and the beaches near Panama City, Florida (approximately 1,200 nests in 1998); (4) a Yucatan nesting subpopulation, occurring on the eastern Yucatan Peninsula, Mexico (approximately 1,000 nests in 1998); and (5) a Dry Tortugas nesting subpopulation, occurring in the islands of the Dry Tortugas, near Key West, Florida (approximately 200 nests per year) (see NMFS 2002).<br/><br/>Aerial beach surveys indicated that about 14,150 females nested in the southeastern U.S. in 1983 (CSTC 1990). In the early 1990s, an estimated 50,000 to 70,000 clutches were laid each year there (Meylan et al. 1995). An estimated minimum of 2200-11,000 individuals occur in summer in waters off the northeastern U.S. (Shoop and Kenney 1992)","viabilityComments":null,"threatImpactComments":"Threats are summarized by Wallace et al. (2011) and National Marine Fisheries Service (2020), presented in order of importance here.<ol> <li>Fisheries bycatch: capture in fishing gear targeting other species. Bycatch occurs in numerous types of fishing, including pelagic and demersal longlines; drift and set nets; bottom and mid-water trawling; fishing dredges; pound nets and weirs; haul and purse seines; pots and traps; and hook and line gear. Illegal, unreported, and unregulated fishing is likely the single greatest source of bycatch.</li> <li>Direct hunting/fishing of turtles or eggs</li> <li>Coastal development of nesting habitat: alteration of coastal environments by construction, dredging, beach modification, etc. Erosion, shoreline structures, and coastal development reduce the availability of suitable nesting habitat. Artificial lighting, beach use, beach debris, and shoreline structures and coastal developments deter nesting females and prevent hatchlings from reaching the sea.</li> <li>Pollution and Pathogens: marine pollution and debris that affect marine turtles (i.e., through ingestion or entanglement, disorientation caused by artificial lights), as well as impacts of pervasive pathogens (for example fibropapilloma virus).</li> <li>Climate change: increasing nesting beach temperatures affecting hatchling sex ratios, sea level rise, storm frequency and intensity affecting nesting habitats, etc.).</li></ol>Threatened through direct exploitation for food (including eggs) and curio materials, incidental take (chiefly by drowning in shrimp trawls), and by habitat degradation, including beach development, beachfront lighting (Peters and Verhoeven 1994, Salmon and Witherington 1995), ocean pollution (including marine debris, which may be ingested), and dredging (direct kills and injuries). Beach armoring, including sea walls, rock revetments, riprap, sandbag installation, groins, and jetties, can result in loss of nesting beaches due to accelerated erosion, prevention of natural beach and dune accretion, and interference with females attempting to reach suitable nesting sites. Beach cleaning operations can destroy nests or produce tire ruts that inhibit movement of hatchlings to sea. The effect of beach restoration may depend on sand type used and subsequent management. Additional threats include predation and/or trampling of eggs and young by raccoons and feral mammals, trampling/crushing of eggs or young by vehicles or human pedestrians, deaths caused by collisions with boats (e.g., in southeastern and southern Florida and shallow coastal bays of the Gulf of Mexico) and intentional attacks by humans (fishermen) (Mitchell 1991). Long-term threats include sea level rise which, coupled with inland urbanization, may reduce available nesting beaches. Since sexual differentiation depends on incubation temperature, there is concern that global warming may result in an imbalance in the sex ratio (Mrosovsky and Provancha 1989). Annual mortality due to drowning in shrimp nets has been estimated at 5000-50,000 in the southeastern U.S.; an additional 550-5500 may die each year from other human activities (CSTC 1990). The fall bottom fishery and black drum fishery may be having adverse effects on loggerheads that use Chesapeake Bay (Mitchell 1991). Susceptible to entanglement and drowning in pound net hedging in Chesapeake Bay (Lutcavage and Musick 1985). In Georgia, predation by the imported fire ant may be a serious threat to eggs and hatchlings (Moulis 1997). See USFWS (1998) for detailed information on certain threats, including beach erosion, beach armoring, beach nourishment, artificial lighting, beach cleaning, increased human presence, recreational beach equipment, exotic dune and beach vegetation, nest loss to abiotic factors, predation, and poaching.","shortTermTrendComments":"Trends differ among the ten recognized global subpopulations, but numbers are declining in some areas. The North West Indian Ocean and South Pacific subpopulations are decreasing, whereas those in the North West Atlantic, South West Atlantic, North Pacific, Mediterranean, and South West Indian Ocean are increasing. Those in the North East Atlantic, North East Indian Ocean, and South East Indian Ocean have unknown trends (Casale and Tucker 2017).<br/><br/>Recent surveys at the major nesting area in Oman (representing about 35% of the global population) indicate a 79% decline between the periods 1985-1996 and 2008-2016 (Willson et al. 2020). The North West Atlantic subpopulation (e.g. those nesting along the southeast coast of the U.S.) declined in the last decades of the twentieth century (CSTC 1990, Taylor 1992, NMFS 2002, Jenkins 2002). However, using all nesting beach datasets in the North West Atlantic region with time series longer than 10 years (with 2013 being the latest available year), Ceriani and Meylan (2017) found that trends ranged from negative to positive, with most negative trends observed in the Florida Peninsular Recovery Unit (35% of the 23 Florida index nesting beaches had negative trends). At the Recovery unit level, there was an overall increase of 35% for the Northern RU, a 2% decrease for the Florida Peninsular RU, a 1% decrease for the Northern Gulf of Mexico RU, and a 53% increase for the Greater Caribbean RU. The overall trend for the North West Atlantic subpopulation was positive (+2%).<br/><br/>Globally, the trend is estimated to amount to a 47 percent decline for the last three generations (Casale and Tucker 2017).","longTermTrendComments":null,"inventoryNeeds":"Identify important non-nesting habitats (foraging, development, wintering).","numberProtEosComments":"Many nesting beaches worldwide are designated for protection, although poaching occurs. Listed threatened by USFWS (F.R. 07-28-78). Required TED use (see \"GPROTNEED\") in some areas (southeastern United States). See NMFS (2001, Federal Register 66:50148-50159) or Jenkins (2002) for a review of proposed new TED regulations.","protectionNeeds":"Restrict human presence on and degradation of nesting beaches and adjacent land and water. Use of TEDs (turtle excluder devices) needs to be mandatory on shrimping vessels from all countries. Beachfront lighting should be banned or converted to turtle-insensitive wavelengths. Take immediate steps to reduce global warming and sea level rise.<br/><br/>See \"Recovery plan for U.S. Pacific populations of the loggerhead turtle (<i>Caretta caretta</i>)\" (draft document was available from National Marine Fisheries Service, Silver Spring, Maryland, and U.S. Fish and Wildlife Service, Portland, Oregon, in 1995).","otherConsiderations":null,"intrinsicVulnerabilityComments":null,"enviromentalSpecificityComments":null},"animalCharacteristics":{"elementGlobalId":105239,"majorHabitat":{"id":1,"majorHabitatDescEn":"Marine","majorHabitatDescEs":"Marino","majorHabitatDescFr":"Marine"},"nonMigrant":false,"localMigrant":true,"longDistanceMigrant":true,"mobilityMigrationComments":"Migrates between nesting beaches and marine waters. At least some temperate zone nesters migrate to tropical waters after the nesting season (Dodd 1990). Females that nest on east coast of Florida migrate to the Gulf of Mexico and West Indies for non-nesting periods. Some individuals in the southeastern U.S. move north in spring (e.g., see Morreale and Standora, no date), south as fall approaches; others apparently remain in Florida waters year-round. Hatchlings from the southeastern U.S. apparently enter drift lines and ride currents to Europe and the Azores and back (Dodd 1990). MtDNA data confirm that juveniles occurring in pelagic habitats of the eastern Atlantic (Azores, Madeira) are derived from nesting populations in the southeastern United States and adjacent Yucatan Peninsula in Mexico (Bolten et al. 1998). <br><br>MtDNA data indicate that stranded individuals along foraging habitat in the northeastern United States from Massachusetts to Virginia originated from three demographically independent nesting areas: northeast Florida/North Carolina, southern Florida, and Quintana Roo (Mexico) (Rankin-Baransky et al. 2001). <br><br>MtDNA data indicate that young occurring along the coast of Baja California derive from nesting areas in Japan and Australia (B. Bowen et al. 1995, Proc. Natl. Acad. Sci. 92:3731-3734); evidently trans-Pacific migrations occur, encompassing several years. <br><br>In North Carolina, within a single year, most multiple-nesting females confined their nesting activities within 4.8 km (Webster and Cook 2001).","foodHabitsComments":"Eats various marine invertebrates (crustaceans, mollusks, sponges, cnidaria, echinoderms, etc.), few plants; also fish (carrion or slow-moving species). Horseshoe crabs are preferred prey in Chesapeake Bay. Spider crabs and rock crabs were important prey at Long Island, New York (Copeia 1993:1176-1180). Adults forage primarily on the bottom (e.g., see Preen 1996, J. Herpetol. 30:94-96), also take jellyfish from surface. Young feed on prey (e.g., gastropods, fragments of crustaceans and sargassum) concentrated at the surface.","animalPhenologyComments":"May bury in bottom mud during cold periods in some areas (e.g., Port Canaveral ship channel off eastern Florida, Gulf of California) (Dodd 1988).","colonialBreeder":true,"length":92,"width":null,"weight":113000,"animalPhenologies":[{"animalCagPhenologyId":100566,"animalPhenology":{"id":2,"animalPhenologyDescEn":"Circadian","animalPhenologyDescEs":"Circadiano","animalPhenologyDescFr":"Circadien","displayOrder":2},"adult":true,"immature":true}],"animalFoodHabits":[{"animalCagFoodHabitsId":101209,"foodHabits":{"id":2,"foodHabitsDescEn":"Piscivore","foodHabitsDescEs":"Piscivore","foodHabitsDescFr":"Piscivore","displayOrder":2},"adult":true,"immature":true},{"animalCagFoodHabitsId":101210,"foodHabits":{"id":3,"foodHabitsDescEn":"Invertivore","foodHabitsDescEs":"Invertívoro","foodHabitsDescFr":"Invertivore","displayOrder":3},"adult":true,"immature":true},{"animalCagFoodHabitsId":101211,"foodHabits":{"id":4,"foodHabitsDescEn":"Herbivore","foodHabitsDescEs":"Herbívoro","foodHabitsDescFr":"Herbivore","displayOrder":4},"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":105239,"eoManagementGroupName":null,"stewardshipOverview":null,"impacts":null,"restorationPotential":"Because so little is known loggerhead population dynamics and demography, it is difficult to assess restoration potential. However, most authors, in discussing conservation strategies, seem optimistic about the loggerhead's recovery if the ongoing population declines can be halted. Turtle excluder devices (TEDs) appear to be effective in reducing mortality associated with the shrimp fishery, improving the outlook for population recovery (Crowder et al. 1995)","siteConservationPlansConsidered":"It is impossible to protect the loggerhead throughout its life cycle due to its expansive range and wandering years at sea. However, nesting beaches can and should be protected. These beaches should be undeveloped, unlighted, virtually unused by humans, and fishing, especially shrimp trawling, should not be allowed near them, especially in the breeding season. These beaches should be carefully managed for the benefit of the loggerhead.","managementMethods":"Worldwide public awareness of plight of sea turtles needs to be improved. 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>The immediate management goal should be to stop the population decline. Although natural mortality contributes to the decline, it is not easy to manipulate. Efforts should be focused on protecting nesting habitat, nesting females, and nests, and on lowering mortality caused by humans. Specific beneficial management activities related to nesting include relocating nests threatened by erosion, restricting beach armoring, closely monitoring beach nourishment, enforcing lighting ordinances, regulating off road vehicles, and protecting nests from pedestrian traffic and beach cleaning equipment by either moving eggs to safer places or marking their presence. Disturbance of nesting females and harvest of adults and eggs should be prevented. <br><br>Lights near beaches may disorient hatchlings (Peters and Verhoeven 1994) and discourage nesting; beach lighting restrictions on nesting baches should include the entire period of darkness (Witherington et al. 1990). If lighting cannot be eliminated, low pressure sodium vapor lights may be the least disruptive to nesting turtles (Witherington 1992). Adding a low light barrier (simulating a dune or dense vegetation) improved hatchling orientation accuracy on urban beach segments exposed to lights in Florida (Salmon et al. 1995). <br><br>In addition to protection and suitable management of nesting habitat, reduction in trawl-related mortality (associated with shrimping), through the use of turtle excluder devices (TEDs, required for offshore shrimpers as of July 1989), seasonal fisheries closures, and reduced tow times, are regarded as primary management needs (CSTC 1990, USFWS 1990, Crowder et al. 1994, Lewison et al. 2003). Use of TEDs by shrimp trawlers theoretically could reduce the capture of sea turtles to 3% of the rate without the TED.  <br><br>TEDs are designed to be installed in shrimp-trawl gear with the purpose of releasing sea turtles and other large objects from nets without releasing shrimp. By November of 1989, six TEDs had been approved by the National Marine Fisheries Service (NMFS), meaning that they are able to exclude at least 97% of the sea turtles otherwise captured and retained in a control trawl without a TED. Use of TEDs should be mandated and regulated from Cape Hatteras to the Texas-Mexican border, as well as all other areas where sea turtles are known to be caught in shrimp trawls. Tow-time limits can reduce the average rate of mortality of sea turtles to a negligible point as tow time is reduced to 60 minutes or less. This can be better than TEDs for areas with a lot of debris. The recommended tow-times are vary seasonally, specifying 40 minutes in the summer and 60 minutes in the winter. Limited time/area closures for turtle \"hot spots\" should be considered. 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). 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. Population models indicate that good compliance with regulations requiring TEDs year-round in all waters of the southeastern United States could allow the population to increase much faster than expected under the \"seasonal offshore\" regulations (Crowder et al. 1994).<br><br>Efforts should be made to avoid sea turtle entrainment in power plant water intakes. Additionally, the use of explosives to remove oil rigs should be prohibited until more is known about its affect on loggerheads. <br><br><br><br>Effort is needed in informing and educating the public on minimizing disturbance to nesting turtles, protecting nests, and rescuing disorientated hatchlings. Mitchell (1991) noted the importance of public education in reducing mortality caused by humans. <br><br>In some areas, predator control may be needed to combat raccoons and other predators whose coastal populations are abnormally high due to food resources being augmented by human refuse. Wire-mesh predator (e.g., raccoon) exclosures around nests have been used in some areas (e.g., Canaveral National Seashore) to enhance reproductive success (1994 End. Sp. Tech. Bull. 19(2):16). However, in Florida, Mroziak et al. (2000) found that predator exclosure cages failed to protect nests and may have attracted them; the authors concluded that reducing predator populations is more effective than using cages to protect nests. See Matthews and Moseley (1990) for examples of interagency cooperation in protecting nesting areas and reducing egg loss to predators. Elimination/control of feral livestock on barrier islands may allow increased production of hatchlings (Shoop et al. 1985). <br><br>Public purchase of undeveloped beaches may be effective in providing prolonged protection of turtles and their habitat. Available lands should be protected before they are lost to development interests. In Florida, 16 km of undeveloped beach from Melbourne Beach to Wabasso Beach is available and should be protected as this is a tremendously important nesting area from a global perspective. Also, the establishment of a marine park at Rancho Nuevo in Mexico would be beneficial. <br><br>Headstarting and captive breeding should remain research tools but should not be used as substitutes for other conservation measures. Eggs relocated to polystyrene incubators have higher hatching success than do eggs in undisturbed nests or eggs relocated to other beach sites (Wyneken et al. 1988). See McGehee (1990) for information on egg incubation procedures. See Mrosovsky and Benabib (1990) for an evaluation of methods for sexing hatchlings. <br><br>See Dodd (1992) for protection recommendations for Florida. <br><br>See recovery plan: Marine Turtle Recovery Team (1984). See also \"Recovery plan for U.S. Pacific populations of the loggerhead turtle (CARETTA CARETTA)\" (NMFS 1998). See USFWS (1998) for detailed information on management and recovery, especially for populations in Florida. <br><br>See Dodd (1988) for further discussion of management strategies.","monitoringMethods":"Monitoring of sea turtles is not an easy task. Currently, the only way of keeping track of individuals over a long period of time is by tagging the hatchlings after they emerge or tagging the females on nesting beaches. A complicating factor is that the tags are readily lost. <br><br>Monitoring of nesting populations can be achieved through aerial and ground surveys of the nesting grounds. This can indicate population trends if carried out over a long period of time; usually at least a decade is required to acquire adequate data.","managementProgramContacts":"One program consists of a joint state, federal, and private effort to provide permanent protection for 15 km of 34 km of high-density sea turtle nesting habitat between Melbourne and Wabasso beaches on the Atlantic coast of east-central Florida. <br><br>State and federal agencies are involved in regulating projects which relocate nests to higher sites on a dune or into a hatchery to combat erosion. <br><br>The NMFS Southeast Regional Office has begun many programs on behalf of the loggerhead. These include regulation development, recovery planning and implementation, information dissemination, TED certification, and permit administration. NMFS also regulates beach nourishment programs. <br><br>Many states, counties, and towns are making progress in mitigating the deleterious effects of light on nesting females and hatchlings. <br><br>The Center for Marine Conservation, Florida Power and Light Co., NMFS, FWS, and environmental groups together have put out a wide variety of material in an effort to educate the public on sea turtle conservation needs. <br><br>MARPOL and other programs to reduce marine pollution are in place and recently have been strengthened. <br><br>The 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":"One management research program is referred to as headstarting, a procedure in which hatchlings are retained in captivity and reared for at least several months with the goal of increasing the juvenile population by reducing hatchling mortality. The effectiveness of this technique is strongly debated. Survivors of such turtles in the wild is documented, but no nesters have ever been found. The practice has been very valuable in increasing the understanding about elements of physiology and behavior of sea turtles. In 1989, Florida terminated its 30-year-old green turtle and loggerhead headstart program because of problems such as skewed sex ratios from artificial incubation, possible interference with imprinting, nutritional deficiencies of hatchlings due to confinement, and possible behavioral modifications. Additionally, the practice is expensive. <br><br>Loggerheads have been successfully reared in captivity from egg to adulthood, and the adults have laid fertile eggs. The ability of such captive-bred turtles to survive and reproduce in the wild, however, is not known. <br><br>Some experimentation with artificial imprinting has been conducted. It is thought that olfactory imprinting on the natal beach may occur on hatchlings. Perhaps the imprinting cues can be altered to a new beach by relocating the eggs, thereby facilitating the creation of new nesting sites and restoration of old ones. <br><br>The Sea Turtle Dredging Task Force, including representatives of the Army Corps of Engineers, the NMFS, the USFWS, the Florida DNR, and the Navy, was created in 1981. They have instituted many different research programs such as an observer program with an on-board biologist to document the take of sea turtles by dredges. Screens have been installed on dredge discharge ports to monitor the presence of sea turtle parts. The task force is involved in an investigation of the configuration and relative threat to sea turtles of various types of dredges and dredge dragheads. Also under investigation are various methods designed to repel turtles from the channel to be dredged or from the vicinity of the dredge. Some turtles are being radio-tracked in navigation channels. Another task force effort is to determine the frequency and distribution of sea turtles in key navigation channels of Florida's coast and elsewhere. <br><br>Research is being performed on the use of low pressure sodium lights on nesting beaches. They seem to have a minimal effect on hatchling orientation, however, they still prompt some concerns.","managementResearchNeeds":"An enlargement of tagging programs and the creation of new ones, paying special attention to the problem of tag loss, will help in gaining much-needed population data. The ecology and movements of hatchlings and young need to be investigated. <br><br>Research on the effects and prevalence of cold stunning should be carried out. Improved resuscitation techniques of comatose turtles should be developed. <br><br>Accurate postmortem techniques need to be developed to determine the role of plastic ingestion on turtle deaths, and documentation is needed of the extent of the problem. Also, information is needed on the effects of petroleum ingestion and fouling. <br><br>Detailed examination of the potential of shrimping in fishing zones and times of the year when damage to turtle populations would be minimal without TED or tow- time restrictions is needed. Improved TEDs should be developed and new alternatives explored. The effectiveness of tow-time limitations needs to be documented. More information is needed on the impact of groundfish trawling, set-net and long-line fishing, gill nets, and pound-net fishing. <br><br>The complex effects of artificial protection of early life stages of sea turtles needs to be determined.","biologicalResearchNeeds":null,"additionalTopics":null},"occurrenceViabilities":[{"eoRankSpecsDetailId":106671,"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":"2020-05-14T02:28:32.230421Z"}],"references":[{"id":121436,"citation":"Alderton, D. 1988. Turtles and tortoises of the world. Facts on File Publications, New York.","shortCitationAuthor":"Alderton","shortCitationYear":1988,"referenceCode":"B88ALD01NAUS","lastModified":"2020-02-25T18:24:27.096237Z"},{"id":143105,"citation":"Bjorndal, K. A., and A. B. Bolten. 1988. Growth rates of juvenile loggerheads, <i>Caretta caretta</i>, in the southern Bahamas. J. Herpetology 22:480-482.","shortCitationAuthor":"Bjorndal and Bolten","shortCitationYear":1988,"referenceCode":"A88BJO01NAUS","lastModified":"2020-02-25T18:24:27.111858Z"},{"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":124270,"citation":"Bolten, A. B., H. R. Martins, K. A. Bjorndal, M. Cocco, and G. Gerosa. 1992. <i>Caretta caretta</i> (loggerhead). Pelagic movement and growth. Herpetological Review 23:116.","shortCitationAuthor":"Bolten et al.","shortCitationYear":1992,"referenceCode":"A92BOL02NAUS","lastModified":"2020-02-25T18:24:27.111858Z"},{"id":215445,"citation":"Bolten, A. B., K. A. Bjorndal, H. R. Martins, T. Dellinger, M. J. Biscoito, S. E. Encalada, and B. W. Bowen. 1998. Transatlantic developmental migrations of loggerhead sea turtles demonstrated by mtDNA sequence analysis. Ecolgical Applications 8:1-7.","shortCitationAuthor":"Bolten et al.","shortCitationYear":1998,"referenceCode":"A98BOL01NAUS","lastModified":"2020-02-25T18:24:27.111858Z"},{"id":128390,"citation":"Bowen, B. W., N. Kamezaki, C. J. Limpus, G. R. Hughes, A. B. Meylan, and J. C. Avise. 1994. Global phylogeography of the loggerhead turtle (<i>Caretta caretta</i>) as indicated by mitochondrial DNA haplotypes. Evolution 48:1820-1828.","shortCitationAuthor":"Bowen et al.","shortCitationYear":1994,"referenceCode":"A94BOW01NAUS","lastModified":"2020-02-25T18:24:27.096237Z"},{"id":117297,"citation":"Carr, A. 1952. Handbook of turtles. Comstock Publishing Associates, Ithaca, New York. 542 pp.","shortCitationAuthor":"Carr","shortCitationYear":1952,"referenceCode":"B52CAR01NAUS","lastModified":"2020-02-25T18:12:49.210733Z"},{"id":1147306,"citation":"Casale, P. 2015a. <i>Caretta caretta</i> (North West Indian Ocean subpopulation). The IUCN Red List of Threatened Species 2015: e.T84127873A84127992. https://dx.doi.org/10.2305/IUCN.UK.2015-4.RLTS.T84127873A84127992.en. Accessed on 29 September 2024.","shortCitationAuthor":"Casale","shortCitationYear":2015,"referenceCode":"N15CAS05NAUS","lastModified":"2024-12-06T23:50:40.5339Z"},{"id":1147307,"citation":"Casale, P. 2015b. <i>Caretta caretta</i> (North East Indian Ocean subpopulation). 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The Canadian population is threatened directly by commercial fishing, particularly bycatch in the pelagic longline fleet, and by loss and degradation of nesting beaches in the southeastern USA and the Caribbean. Other threats include bycatch from bottom and midwater trawls, dredging, gillnets, marine debris, chemical pollution and illegal harvest of eggs and nesting females.<br/><br/>Status history: Designated Endangered in April 2010.","usesaDate":"2011-09-22","interpretedUsesa":null,"usesaComments":"As of May 2022, the NMFS status of the loggerhead turtle are as follows (see https://www.fisheries.noaa.gov/species/loggerhead-turtle):<br/><br/>Endangered: North Pacific Ocean DPS, Mediterranean Sea DPS, Northeast Atlantic Ocean DPS, North Indian Ocean DPS, South Pacific Ocean DPS<br/>Threatened: Northwest Atlantic Ocean DPS, South Atlantic Ocean DPS, Southeast Indo-Pacific Ocean DPS, Southwest Indian Ocean DPS","completeDistribution":true,"synonyms":[],"infraspeciesList":[],"ebarId":null,"ebarCanadianScope":false,"ebarGlobalScope":false,"ebarKbaGroup":"Amphibians and Reptiles","caGeneralStatusId":"GS000803"},"speciesCharacteristics":{"elementGlobalId":105239,"reproductionComments":"In the southeastern U.S., mating occurs late March-early June. Lays 1-9 clutches (mostly 2-6) of about 45-200 eggs (average 120) at intervals of about 2 weeks, mostly every 2-3 years. Nests mainly at night, often at high tide. In the U.S., nests late April-early September, peak in June. Eggs hatch in about 7-11 weeks (generally 8-9 weeks in the southeastern U.S.). Egg mortality may result from predation, beach erosion, invasion of clutches by plant roots, crushing by off-road vehicles, or flooding by sea water overwash or excessive rainfall. Sex of hatchlings is affected by incubation temperature, with warmer temperatures resulting in a preponderance of females and cooler temperatures producing mainly or only males. Hatchlings emerge from nest a few days after hatching, typically during darkness. Sex ratio of hatchlings and immatures in Atlantic coastal waters of U.S. is strongly biased toward females (Wibbels et al. 1991, Mrosovsky and Provancha 1992). Females are sexually mature at an average age of about 15-30 years in the southeastern U.S. (but see Bjorndal and Bolten [1988] for information on juvenile growth rates that suggests earlier age of maturity; see also Klinger and Misick, Copeia 1995:204-209, and Zug et al., Copeia 1995:484-487, for growth rate and age-at-maturity information). Females are reproductively active over a period of about 30 years (CSTC 1990). Nesting density reaches nearly 450 nests/km in some areas of Florida (Dodd 1992).","ecologyComments":"Does not form schools but local concentrations may occur at sea or near nesting beaches. <br><br>Of every thousand hatchlings, only a few are believed to survive to adulthood; this is characteristic even of stable populations (Dodd 1988). In Georgia, annual survivorship of adult females was 0.81, juveniles 0.70-0.94; see Iverson (1991) for a compilation of survivorship data. Maximum reproductive life span 32 years (Frazer 1983). <br><br>Among a wide array of animals that eat loggerhead eggs, raccoons are the most important predators on eggs in the southeastern U.S.; on some beaches they have been responsible for more than 90% of nest mortality (Dodd 1988). Organisms attached to the shell are not known to pose a significant threat. <br><br>Cold stunning in estuaries (e.g., Long Island Sound) sometimes can result in significant mortality. See Witherington and Ehrhart (1989) for information on cold stunning in Florida. <br><br>Data on heavy metal concentrations in eggs support the hypothesis that the western Atlantic population is composed of demes (Stoneburner et al. 1980).","habitatComments":"Open sea to more than 500 miles from shore, mostly over continental shelf, and in bays, estuaries, lagoons, creeks, and mouths of rivers; mainly warm temperate and subtropical regions not far from shorelines. Off North Carolina, loggerheads inhabited waters of 13-28 C (available range 5-32 C) (Coles and Musick 2000). Adults occupy various habitats, from turbid bays to clear waters of reefs. Subadults occur mainly in nearshore and estuarine waters. Hatchlings move directly to sea after hatching, often float in masses of sea plants (Sargassum); may remain associated with sargassum rafts perhaps for 3-5 years. In Chesapeake Bay, occurs mainly in deeper channels, usually at river mouths or in the open bay. <br><br>Nesting occurs usually on open sandy beaches above high-tide mark, seaward of well-developed dunes. Nests primarily on high-energy beaches on barrier strands adjacent to continental land masses in warm temperate and subtropical regions; steeply sloped beaches with gradually sloped offshore approaches are favored (CSTC 1990). Renesting generally occurs at the same beach or within a few km; generally returns to the same area in subsequent years if habitat remains suitable. Individuals sometimes change to different nesting beach within a single nesting season; has changed to sites up to several hundred km away (see Eckert et al. 1989). Maximum hatching success and hatchling size occur when sand moisture level is about 25%. In Florida, nesting on urban beaches was strongly correlated with the presence of tall objects (trees, buildings), which apparently shield the beach from city lights (Salmon et al. 1995). See Garmestani et al. 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