{"elementGlobalId":103386,"circumscripConfidence":{"id":3,"circumscripConfidenceDescEn":"3 - Weak","circumscripConfidenceDescEs":"3 - Débil","circumscripConfidenceDescFr":"3 – Faible"},"classificationLevel":{"id":8,"classificationLevelNameEn":"Subspecies","classificationLevelNameEs":"Subespecie","classificationLevelNameFr":"Sous-espèce"},"classificationStatus":{"id":1,"classificationStatusDescEn":"Standard","classificationStatusDescEs":"Estándar","classificationStatusDescFr":"Standard"},"iucn":null,"nameCategory":{"id":1,"nameCategoryDescEn":"Vertebrate Animal","nameCategoryDescEs":"Animal vertebrado","nameCategoryDescFr":"Animal vertébré","nameTypeCd":"A","nameTypeDesc":"Zoological"},"rankMethodUsed":{"id":1,"rankMethodUsedDescEn":"Legacy Rank calculation - Excel v3.1x","rankMethodUsedDescEs":null,"rankMethodUsedDescFr":null,"rankMethodUsedExternalDescEn":"Ranked by calculator","rankMethodUsedExternalDescEs":null,"rankMethodUsedExternalDescFr":null},"formattedScientificName":"<i>Sternula antillarum athalassos</i>","scientificName":"Sternula antillarum athalassos","scientificNameAuthor":"(Burleigh and Lowery, 1942)","primaryCommonName":"Interior Least Tern","relatedItisNames":null,"uniqueId":"ELEMENT_GLOBAL.2.103386","elcode":"ABNNM08102","conceptRefFullCitation":"American Ornithologists' Union (AOU). 1957. The AOU check-list of North American birds, 5th ed. Port City Press, Inc., Baltimore, MD. 691 pp.","conceptName":"<i>Sterna albifrons athalassos</i>","taxonomicComments":"Formerly (AOU 1983, 1998) included in the genus <i>Sterna </i>but separated on the basis of genetic data that correspond to plumage patterns (Bridge et al. 2005) (AOU 2006). The American Ornithologists’ Union (AOU) recognizes three subspecies: <i>S. a. browni</i> from California, the Eastern, <i>S. a. antillarum</i>, and the Interior, <i>S. a. athalassos</i> (AOU 1957).<br/><br/>Massey (1976) evaluated morphological, vocal, and behavioral characteristics and concluded that nominal subspecies <i>antillarum </i>and <i>browni </i>are indistinguishable. Thompson et al. (1992) examined morphological and electrophoretic variation and found little evidence of differentiation among populations of the nominal subspecies <i>antillarum</i>, <i>athalassos</i>, and <i>browni</i>; they recommended that the subspecific taxonomy of the <i>S. antillarum</i> complex be reassessed. Johnson et al. (1998) used a quantitative colorimetry analysis to study variation among <i>antillarum, athalassos</i>, and <i>browni </i>and found differences significant enough to warrant the validity of the taxa and their importance as entities for conservation.","roundedGRank":"T3","conservationStatusFactorsEditionDate":"2018-11-29","conservationStatusFactorsEditionAuthors":"Priscilla H.C. Crawford","primaryCommonNameLanguage":"EN","recordType":"SPECIES","elementNationals":[{"elementNationalId":162826,"classifConfidence":null,"nation":{"id":225,"nameEn":"United States","nameEs":"Estados Unidos","nameFr":"États-Unis","isoCode":"US","region":"United States"},"roundedNRank":"N3","elementSubnationals":[{"elementSubnationalId":389066,"subnation":{"id":39,"nameEn":"New Mexico","nameEs":"Nuevo 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populations of the Least Tern were formerly well distributed within the Mississippi Basin. Range-wide declines occurred until the initiation of management of nesting habitat on the Mississippi and Arkansas Rivers by the US Army Corps of Engineers (USACE) and conservation partnerships on the Platte River. Current viable populations are reliant on continued management of habitat by the USACE (USFWS 2014). These populations have seen a rebound, but habitat quality continues to decline on the periphery of the geographic range. Interior subspecies is generally not recognized as a distinct taxonomic entity, but continues to be listed as a Federally Endangered population by the USFWS.","grankReviewDate":"2018-11-29","rankInfo":{"elementGlobalId":103386,"aooPercentGood":null,"enviromentalSpecificity":null,"intrinsicVulnerability":null,"longTermTrend":null,"numberEos":{"id":15,"numberEosDescEn":"> 300","numberEosDescEs":"> 300","numberEosDescFr":"> 300"},"numberGoodEos":null,"numberProtEos":null,"popSize":{"id":28,"popSizeDescEn":"2500 - 100,000 individuals","popSizeDescEs":"De 2.500 a 100.000 individuos","popSizeDescFr":"De 2 500 à 100 000 individus"},"rangeExtent":{"id":33,"rangeExtentDescEn":"200,000-2,500,000 square km (about 80,000-1,000,000 square miles)","rangeExtentDescEs":"200.000 a 2.500.000 kilómetros cuadrados (aproximadamente 80.000 a 1.000.000 millas cuadradas)","rangeExtentDescFr":"De 200 000 à 2 500 000 km carrés (de 80 000 à 1 000 000 miles carrés approximativement)"},"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":"BREEDING: Historically throughout the Colorado, Red, Arkansas, Missouri, Ohio, and Mississippi river systems. Has been eliminated from much of former habitat. Now breeds locally on the Missouri River through eastern Montana, North Dakota, South Dakota, and Nebraska; on the Platte River in Nebraska; on the Arkansas and Canadian Rivers through Oklahoma; on the Arkansas River through Arkansas to the Mississippi; on the Mississippi and Ohio River from western Indiana to Louisiana, and on the Red River along the borders of Oklahoma and Texas and into Louisiana. Sporadic observations of small colonies have been noted in eastern Colorado, central Kansas, eastern New Mexico, and western, southern, and central Texas (Lott et al. 2013).<br /><br />NON-BREEDING: Least terns winter primarily in marine coastal areas. It is likely that interior populations mix with other populations during winter months. Because interior birds are morphologically indistinguishable and recovery rate of banded birds is low, biologists are not capable of defining winter areas for Atlantic and Gulf coastal populations versus interior populations. Least terns winter throughout western coast of southern Mexico, and along eastern coasts of Mexico, Central, and South America, extending south to southern Brazil. First year birds may remain in wintering areas before migrating north for breeding during their second year (Thompson et al. 1997).","areaOfOccupancy":null,"areaOfOccupancyComments":null,"numberEosComments":null,"popSizeComments":"The last comprehensive survey of the interior populations was in 2005 with 17,591 individuals observed throughout the range. Partial surveys were conducted in 2010 (21,855 individuals observed), 2011 (15,403 individuals observed), and 2012 (13,855 individuals observed). The majority of the increase in birds in the past 20 years is a result of increased populations on the Mississippi River. Populations on the Platte, Missouri, Ohio, and Arkansas River systems have remained low or declined further. Although the numbers have exceeded the range-wide recovery target as designated in the USFWS Recovery Plan (1990), the majority of the specific river system target numbers fall short (USFWS 2014).","viabilityComments":null,"threatImpactComments":"Primary threats are loss of suitable nesting habitat on open sandbars and islands due to channelization and flood control of rivers systems, hydrological changes due to groundwater usage and climate change, vegetation encroachment on sandbars, sand and gravel mining activities, human disturbance by those recreating along the rivers, and predation.<br /><br />CHANNELIZATION AND FLOOD CONTROL: Channelization of river systems reduces the amount of exposed sand and restricts the sandbar formation processes, therefore reducing the amount of habitat available for colony formation (Alexander et al. 2018). Scouring floods are a necessary process to maintain bare sandbar habitat. By controlling flooding, dams and other structures reduce the potential of flood events that maintain suitable habitat.<br /><br />HYDROLOGICAL CHANGES: Increased groundwater usage has lowered the water table throughout the Great Plains (McGuire 2017), flow rates for rivers in the Great Plains have declined, and stream drying is becoming common throughout the region (Kustu, Fan, Robock 2010). These hydrologic changes negatively affect sandbar maintenance and formation. Stream drying reduces the fish availability for Least Tern foraging (Perkin et al. 2017).<br /><br />VEGETATION ENCROACHMENT: Reduction of scouring floods due to flood control or decreases in stream flow allow for vegetation encroachment on sandbars. Least terns prefer nesting habitat devoid of all vegetation and at least 70m from trees and shrubs over 2m (Lott et al. 2013). When flooding is infrequent, sandbars become more resistant to scouring due to the increased vegetation coverage by woody species, both native and exotic. In western parts of the Interior Least Tern range, salt cedar (<i>Tamarix </i>spp.) has become well established on along river channels and has withstood high water events. Native willow (<i>Salix</i> spp.) and cottonwood (<i>Populus deltoides</i>) also become well established and stabilize the sandbars.<br /><br />SAND AND GRAVEL MINING: Mining operations regularly occur on and create areas of bare sand and gravel along rivers that are suitable nesting habitat for Interior Least Terns. Most operators are unaware of the birds attempting to nest on the bare ground within their work zone. Programs have successfully worked with miners to monitor and protect nesting sites (Brown et al 2018). However, cooperation is a continual process that requires significant contribution of time and effort by both dedicated conservationists and willing industry partners. Although sand and gravel mining operations may cooperate with conservation efforts, removal of material from the floodplain will lower the sandbar elevation and increasing the likelihood that nesting sites will be inundated during minor high water events (Farnsworth et al. 2017).<br /><br />HUMAN DISTURBANCE: Wide and shallow prairie river channels are common areas for off-road vehicle recreation. Interior Least Tern nests are well camouflaged and are easily overlooked by drivers. Vehicles can directly crush nests and chicks, but nests can also be abandoned by repeated disturbance to the colony by traffic (Carney and Sydeman 1999).<br /><br />PREDATION: Because habitat quality is decreasing, vulnerability to nest predation is increasing for Interior Least Terns. Vegetation encroachment allows predators to approach nesting birds while being hidden undercover. Human habitation near colony sites may be increasing generalist, urban, and exotic species, such as raccoons, coyotes, Norway rats, domestic cats, and feral hogs that are predators of ground nesting birds (Carney and Sydeman 1999).","shortTermTrendComments":"The last comprehensive survey of the interior populations was in 2005 with 17,591 individuals observed throughout the range. Partial surveys were conducted in 2010 (21,855 individuals observed), 2011 (15,403 individuals observed), and 2012 (13,855 individuals observed). The majority of the increase in birds in the past 20 years is a result of increased populations on the Mississippi River, due to a change in channel design implemented by the USACE. Populations on the Platte, Missouri, Ohio, and Arkansas River systems have remained low or declined further. Although the numbers have exceeded the range-wide recovery target as designated in the USFWS Recovery Plan, the majority of the specific river system target numbers fall short (USFWS 2014).","longTermTrendComments":null,"inventoryNeeds":null,"numberProtEosComments":null,"protectionNeeds":null,"otherConsiderations":null,"intrinsicVulnerabilityComments":null,"enviromentalSpecificityComments":null},"animalCharacteristics":{"elementGlobalId":103386,"majorHabitat":{"id":3,"majorHabitatDescEn":"Terrestrial","majorHabitatDescEs":"Terrestre","majorHabitatDescFr":"Terrestre"},"nonMigrant":false,"localMigrant":false,"longDistanceMigrant":false,"mobilityMigrationComments":null,"foodHabitsComments":null,"animalPhenologyComments":null,"colonialBreeder":false,"length":null,"width":null,"weight":null,"animalPhenologies":[],"animalFoodHabits":[]},"occurrenceDelineations":[{"eoSpecsDetailId":1093,"locationUseClass":{"id":2,"locationUseClassDescEn":"Breeding","locationUseClassDescEs":"En reproducción","locationUseClassDescFr":"Reproduction","displayOrder":2},"eoSpecGroupName":"Gulls and Terns","subtypes":null,"inferredExtentDistance":null,"inferredExtentNotes":"Inferred extent not appropriate, since foraging areas often separated by a considerable distance from breeding colony.","minimumEoCriteria":"Evidence of historical breeding, or current and likely recurring breeding, at a given location, minimally a reliable observation of one or more breeding pairs in appropriate habitat. Be cautious about creating EOs for observations that may represent single breeding events outside the normal breeding distribution.","mappingGuidance":null,"separationBarriers":"None.","separationDistanceUnsuitableHabitatat":5.0,"separationDistanceSuitableHabitatat":5.0,"altSeparationProcedure":null,"separationJustification":"Occurrences include nesting areas and associated nesting-season foraging areas (regardless of how far apart they are), but separation distance pertains to nesting areas (breeding colonies). Thus different breeding occurrences may overlap if birds from different nesting areas forage in the same area. Separation distance is not intended to delineate demographically independent populations or metapopulations (such units would be quite large). Instead, separation distance is a compromise between the high mobility of these birds (see following) and the need for occurrences that are of practical size for conservation/management use. <br /><br />California Gulls foraged an average of 17.4 kilometers from colony (Baird 1976); maximum foraging distances ranged from 32 to 61 kilometers (Rothweiler 1960, Baird 1976). Ring-billed Gulls foraged an average of 11 km from colony (Baird 1977). Least Terns foraged up to 3-12 kilometers from nests (summarized in Thompson et al. 1997). Forster's Terns has a reported feeding radius of 3.2 kilometers (Van Rossem 1932). Black Terns foraged up to 10 kilometers from nests, over continuous suitable but unoccupied habitat (M. A. Stern, pers. comm. 1998). Caspian terns in a colony at the mouth of the Columbia River: 90% of adults foraged within 21 kilometers (Collis et al. 1999).","versionDate":"2004-07-21","versionAuthor":"Cannings, S., and G. Hammerson","versionNotes":null,"lastModified":"2020-04-30T02:05:56.849048Z"},{"eoSpecsDetailId":1095,"locationUseClass":{"id":3,"locationUseClassDescEn":"Nonbreeding","locationUseClassDescEs":"No reproducción","locationUseClassDescFr":"Non-reproduction","displayOrder":3},"eoSpecGroupName":"Gulls and Terns","subtypes":"Foraging Concentration Area","inferredExtentDistance":null,"inferredExtentNotes":null,"minimumEoCriteria":"Evidence of recurring presence of wintering flocks (including historical); and potential recurring presence at a given location, minimally a reliable observation of 25 birds in appropriate habitat. Occurrences should be locations where the species is resident for some time during the appropriate season; it is preferable to have observations documenting presence over at least 20 days annually. Be cautious about creating EOs for observations that may represent single events.","mappingGuidance":null,"separationBarriers":"None.","separationDistanceUnsuitableHabitatat":5.0,"separationDistanceSuitableHabitatat":5.0,"altSeparationProcedure":null,"separationJustification":"Separation distance somewhat arbitrary; set such that occurrences are of managable size for conservation purposes. Occurrences are defined primarily on the basis of areas supporting concentrations of foraging birds, rather than on the basis of distinct populations.","versionDate":"2002-04-16","versionAuthor":"Cannings, S.","versionNotes":"Includes all inland-nesting gulls and terns, in the genera LARUS, STERNA, and CHLIDONIAS.","lastModified":"2020-04-30T02:05:56.849048Z"},{"eoSpecsDetailId":1094,"locationUseClass":{"id":4,"locationUseClassDescEn":"Migratory stopover","locationUseClassDescEs":"Parada migratoria","locationUseClassDescFr":"Halte migratoire","displayOrder":5},"eoSpecGroupName":"Gulls and Terns","subtypes":null,"inferredExtentDistance":null,"inferredExtentNotes":null,"minimumEoCriteria":"Evidence of recurring presence of migrating flocks (including historical); and potential recurring presence at a given location, minimally a reliable observation of 50 birds in appropriate habitat. Occurrences should be locations where the species is resident for some time during the appropriate season; it is preferable to have observations documenting presence over at least 7 days annually. Be cautious about creating EOs for observations that may represent single events.","mappingGuidance":null,"separationBarriers":"None.","separationDistanceUnsuitableHabitatat":5.0,"separationDistanceSuitableHabitatat":5.0,"altSeparationProcedure":null,"separationJustification":"Separation distance somewhat arbitrary; set such that occurrences are of managable size for conservation purposes. Occurrences are defined primarily on the basis of areas supporting concentrations of foraging birds, rather than on the basis of distinct populations.","versionDate":"2004-04-26","versionAuthor":null,"versionNotes":null,"lastModified":"2020-04-30T02:05:56.849048Z"},{"eoSpecsDetailId":156346,"locationUseClass":{"id":6,"locationUseClassDescEn":"Staging","locationUseClassDescEs":"Entorno","locationUseClassDescFr":"Rassemblement","displayOrder":7},"eoSpecGroupName":"Gulls and Terns","subtypes":null,"inferredExtentDistance":null,"inferredExtentNotes":null,"minimumEoCriteria":"Evidence of flocks resting, roosting, and/or feeding young at a given location prior to breeding or after breeding has been completed. Staging may occur near the breeding site, preceding or following major migratory movements such as oceanic crossings, or it may occur after individuals have departed on migration, but before they have arrived at their final destination (a \"stopover\"). Staging may occur at sites also used for breeding, but often does not. Staging habitat may be ephemeral. For Common/Roseate Terns in Massachusetts, a minimum of 100 individuals in appropriate habitat is used.","mappingGuidance":null,"separationBarriers":null,"separationDistanceUnsuitableHabitatat":5.0,"separationDistanceSuitableHabitatat":5.0,"altSeparationProcedure":null,"separationJustification":"In Massachusetts, staging areas are separated somewhat arbitrarily, often by jurisdictional or property boundaries, as are nesting areas for coastal birds.","versionDate":"2017-01-10","versionAuthor":"Mostello, C. S.","versionNotes":null,"lastModified":"2020-04-30T02:05:56.849048Z"},{"eoSpecsDetailId":156347,"locationUseClass":{"id":15,"locationUseClassDescEn":"Adult foraging area","locationUseClassDescEs":"Zona de alimentación de adultos","locationUseClassDescFr":"Aire d’alimentation adulte","displayOrder":15},"eoSpecGroupName":"Gulls and Terns","subtypes":null,"inferredExtentDistance":null,"inferredExtentNotes":null,"minimumEoCriteria":"Applies to both adults and juveniles. Evidence of one or more individuals seeking food in suitable habitat. Evidence of prey capture is not a prerequisite, as importance of a given location for foraging may vary temporally with shifting prey.","mappingGuidance":null,"separationBarriers":null,"separationDistanceUnsuitableHabitatat":5.0,"separationDistanceSuitableHabitatat":5.0,"altSeparationProcedure":null,"separationJustification":"Scientific basis for assigning foraging separation distances is weak because terns are widespread across the Massachusetts coast and highly mobile. Most gaps in foraging observations likely reflect lack of survey effort.","versionDate":"2017-01-10","versionAuthor":"Mostello, C. S.","versionNotes":null,"lastModified":"2020-04-30T02:05:56.849048Z"}],"plantCharacteristics":null,"elementManagement":{"elementGlobalId":103386,"eoManagementGroupName":null,"stewardshipOverview":"From the Interior Least Tern (<i>Sternula antillarum</i>) 5-Year Review Summary and Evaluation (USFWS 2014):<br />“At least some proportion of Interior Least Tern (ILT) range-wide increase is due to increased awareness, survey efforts, management, and protection. ILT have colonized numerous anthropogenic sites (~15% of sites throughout their range, such as sand pits, rooftops, reservoirs, industrial sites), and the persistence of some of these are reliant upon aggressive management (e.g., predator or vegetation control) and protection (e.g., seasonal avoidance).<br /><br />ILT nesting habitat availability and quality are primarily controlled by stochastic events (droughts and floods) affecting river flow and habitat quantity and quality (Sidle et al. 1992). Productivity peaks may also be influenced by stochastic drought events or cycles in some drainages. For example, despite severely altered flow regimes and aggressive ILT habitat management in the Missouri River, ILT distribution and population size have remained relatively stable over the period of record. Evidence suggests that habitat condition in this drainage, as well as annual ILT numbers and productivity, are strongly influenced by current hydrologic patterns. While periodic major flow events reset nesting habitat and the forage base, annual reservoir operations can provide some ILT habitat suitability during drought years. On the Mississippi River, channel training structures (dike fields) and their potential to lead to vegetation encroachment of ILT sandbar habitat were considered causes of decline and imminent threats to the species (Smith and Stuckey 1988). However, population estimates have increased from &lt;500 birds occupying a short reach of the river in 1985, to &gt;10,000 nesting birds/year along &gt;800 mi of river channel over the past decade (Jones 2012). Most ILT colonies on the Mississippi River are associated with dike fields, which create 39 higher sandbars with less exposure to flooding during the summer nesting season. Current management practices on the Mississippi River include new dike designs incorporating notches toward the landward end, allowing flow to isolate nesting bars through most of the nesting season (USACE 2008, USFWS 2012, USACE 2013). Additionally, there is an aggressive program to build notches into existing dikes during maintenance activities (DuBowy 2011, USACE 2013). In other navigation systems that require maintenance dredging (e.g., lower Ohio, Red, and Arkansas rivers), it is becoming standard practice to use the dredged material to build or replenish islands, which are being utilized for nesting by ILT (Ciuzio et al. 2005, Fischer 2012). Reservoir storage and releases have also been modified to minimize impacts and benefit ILT. In the Arkansas and Red river drainages, seasonal pool plans are considered to allow extended water storage to provide minimum flow requirements during the late ILT nesting season (USACE 2002). On the Loup River, ILT forage species are benefitted by the maintenance of minimum flows into a channel bypass reach (Loup Power District 2012). In the Missouri River, the USACE has historically monitored and managed ILT nesting areas and reservoir releases to reduce impacts to nesting birds (USACE 2007). Anthropogenic changes in some river drainages supporting ILT may also have benefited the bird in ways that have partially compensated for habitat losses. For example, in the Lower Mississippi River, impoundment of the major tributaries and channelization of the river have resulted in earlier and shorter duration spring and summer high water events (Schramm 2004), possibly reducing egg and chick flood related mortality events, extending the nesting season, and increasing re-nesting opportunities. Dam construction in arid regions unsuitable for the species allowed expansion of the ILT range.”","impacts":null,"restorationPotential":null,"siteConservationPlansConsidered":null,"managementMethods":null,"monitoringMethods":null,"managementProgramContacts":null,"monitoringProgramContacts":null,"managementResearchPrograms":null,"managementResearchNeeds":null,"biologicalResearchNeeds":null,"additionalTopics":null},"occurrenceViabilities":[{"eoRankSpecsDetailId":104870,"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":"2020-05-14T02:23:58.741935Z"}],"references":[{"id":105760,"citation":"American Ornithologists' Union (AOU). 1957. 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