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with increasing populations in many areas. Since the early 1970s, captive breeding and reintroduction programs have had some success in North America, and reproductive failure due to pesticide contamination has been reduced so that it is no longer a serious threat in most areas. Populations in North America have recovered in some areas and are increasing in most other areas. Populations increasing in northern Eurasia.","grank":"G4","rankInfo":{"elementGlobalId":102654,"aooPercentGood":null,"enviromentalSpecificity":null,"intrinsicVulnerability":null,"longTermTrend":null,"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":33,"popSizeDescEn":"10,000 to >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":44,"shortTermTrendDescEn":"Increase of >10%","shortTermTrendDescEs":"Aumento de >10%.","shortTermTrendDescFr":"Augmentation de >10 %"},"threatImpactAssigned":null,"rangeExtentComments":"Nearly cosmopolitan; breeds on every continent except Antarctica; absent from high mountains, desert regions of Africa, Asia, and Australia, and from most tropical forests; occasionally reaches Hawaii.  In North America, much recovery of populations has occurred, but the large area extending from the western Cascades of Oregon and Washington to the eastern slope of the Big Horn Mountains of Wyoming and Montana and north into the southern provinces of Canada still was largely unoccupied in the early 1990s (The Peregrine Fund 1992).","areaOfOccupancy":null,"areaOfOccupancyComments":null,"numberEosComments":"See GABUNDCOM.","popSizeComments":"Rangewide estimates not available.  Subspecies CALIDUS: breeding poulation across northern Eurasia has been estimated at 3652 territorial pairs (95% confidence interval 2282 to 5018 pairs) (Quinn and Kokorev 2000).  North America: In the early 1990s, the North American population totaled several thousand breeding pairs, including about 700 known territorial pairs in the coterminous U.S. (estimated total about 890 pairs).  Subspecies PEALEI: An estimated 600 breeding pairs are believed to occur in Alaska (Ambrose et al. 1988) and an additional 100 pairs in British Columbia (Munro 1988).  Subspecies ANATUM: In 1998, there were at least 193 breeding pairs in the eastern United States, 32 in the midwest, 535 in the western region, and 269 in the Pacific coast region (USFWS 1999). In Alaska, there are a minimum of 301 breeding pairs (USFWS 1999). In Canada, 319 breeding pairs were located in 1995 (USFWS 1999). Mexico has not been surveyed adequately, but at least 70 nest sites were occupied there in the late 1980s and early 1990s (USFWS 1999).  Subspecies TUNDRIUS: In Greenland, there were approximately 1000-2000 breeding pairs in the early 1990s (Mattox, in USFWS 1993). Alaskan nesting population was estimated at 200-250 pairs in the early 1990s. Additional pairs in the Northwest Territories and elsewhere bring the total up to probably several thousand breeding pairs.","viabilityComments":null,"threatImpactComments":"Threats include loss of wetland habitat of primary prey, poachers robbing nests, shooting by hunters, and food chain contamination from use of persistent pesticides.  Pesticide-caused reproductive failure now apparently is rare or absent in northern populations, though organochlorine levels in the environment are still high in some areas (e.g., New Mexico, Hubbard and Schmitt 1988; see also Peakall 1990; see Banasch et al. 1992 for information on contaminants in prey in Panama, Venezuela, and Mexico). Court (1993) studied the eggs of <i>F. p. anatum </i>in Alberta, Canada between 1983 and 1992, and found that high DDE levels still occurred in some eggs, and that 28 percent of the eggs were still thinner than critical thicknesses considered essential for successful reproduction. <br><br>Also, eggshell thickness in New Jersey declined in the 1980s, suggesting that falcons continue to be exposed to environmental contaminants (Steidl et al. 1991).  Reintroduced populations in some areas of the eastern U.S. (e.g., barrier islands of the mid-Atlantic states) may be threatened by increasing human disturbance and use of nesting habitat (Byrd and Johnston 1991).","shortTermTrendComments":"Populations in the Northern Hemisphere declined drastically from the 1940s to the 1970s due to DDT and its breakdown products, notably DDE, in the environment. During the 1930s and 1940s there were at least 200 breeding pairs in the eastern United States. By the mid-1960s these were all inactive (U.S. Fish and Wildlife 1993). Populations were reduced by an estimated 80-90% in the western U.S. by the mid-1970s; the decline in Alaska probably was no more than 50% (The Peregrine Fund 1992). Populations have been recovering, aided by reintroductions in some areas.  In the early 1980s, continent-wide population was stable, but local increases and declines were continuing (see White et al. [1990] for 1980 status in specific areas). See also Cade et al. (1988) and Palmer (1988). Eastern U.S. population was about 210 active nests and 350 pairs in the 1930s and 1940s; population dropped to zero breeders by the mid-1960s, largely the result of eggshell thinning caused by pesticide and PCB poisoning. Populations increased after U.S. DDT ban and initiation of reintroduction efforts. Populations in Alaska, and the Yukon and Northwest Territories evidently have recovered.  In interior Alaska, numbers increased about 3-fold from the mid-1970s to the early 1990s; pesticide levels have been decreasing and in the early 1990s were well below levels at which reproduction is impaired. Populations increased from 1985 to 1990 in the Yukon Territory, but full occupancy of the historic range had not yet occurred. Populations in the Mackenzie River valley increased from 1985 to 1990, but little is known of population trends in the boreal forest east of the Mackenzie valley (USFWS 1991).  Subspecies TUNDRIUS: In the Northwest Territories, populations are stable or increasing in all surveyed areas (e.g., see Shank et al. 1993); some organochlorine contamination remains, but falcons are reproducing well. In Quebec, breeding performance and habitat occupancy have increased greatly since the 1970s. Overall, in Canada, populations are stable or increasing (Holroyd and Banasch 1995), and there is a continuing danger of organochlorine contamination (Bromley, 1992 COSEWIC report). In Greenland, habitat occupancy had increased to about 90% in 1990 (USFWS 1991). See USFWS (1993) for additional documentation of the recovery of this subspecies.  In Alaska, the number of pairs of subspecies ANATUM and TUNDRIUS both have more than doubled in some areas, without the aid of releases (The Peregrine Fund 1992). Censuses indicate that subspecies TUNDRIUS throughout its range (USFWS 1994) and subspecies ANATUM in Alaska and the Yukon and Northwest Territories have recovered.  A significant increase was recorded in migration counts in northeastern North America, 1972-1987 (Titus and Fuller 1990).  With the exception of the central and western prairie provinces, reported to have recovered throughout much of Canada (The Peregrine Fund 1992). Stable or increasing in northern and western Canada; numbers remain low in southern Canada (Murphy 1990); subspecies PEALEI (breeds along British Columbia and Alaska coasts) and subspecies TUNDRIUS (breeds in arctic, winters in Latin America) seem secure (Peakall 1990).  The Peregrine Fund (1992) recommended that the peregrine, including both subspecies in Alaska be delisted in all western states except Idaho, Montana, Oregon, Washington, and Wyoming (where a change to Threatened status was recommended).  Subspecies CALIDUS: Declined in northern Eurasia during period of intensive organochlorine pesticide use, but now increasing (Quinn and Kokorev 2000).","longTermTrendComments":null,"inventoryNeeds":null,"numberProtEosComments":"Protected in the United States and Canada under the Migratory Bird Treaty and endangered species legislation. Hundreds of EOs are in wildlife refuges, national, state, and provincial parks, and remote wilderness areas.  The arctic peregrine is currently listed under Appendix 1 of The Convention on International Trade in Endangered Species (CITES), an international agreement that restricts trade in rare and endangered species.  Grand Canyon National Park, Arizona, has the largest nesting population on a single land management unit in the contiguous U.S. (Brown et al. 1992).","protectionNeeds":"Continue efforts to protect birds from environmental contaminants.","otherConsiderations":"Large scale captive breeding programs have produced many birds for reintroduction.","intrinsicVulnerabilityComments":null,"enviromentalSpecificityComments":null},"animalCharacteristics":{"elementGlobalId":102654,"majorHabitat":{"id":3,"majorHabitatDescEn":"Terrestrial","majorHabitatDescEs":"Terrestre","majorHabitatDescFr":"Terrestre"},"nonMigrant":true,"localMigrant":true,"longDistanceMigrant":true,"mobilityMigrationComments":"Populations nesting in northern latitudes are highly migratory; those nesting in northern maritime climates, at mid-latitudes, and in the Southern Hemisphere much less so (Cade 1982). Tundra breeders migrate farthest, bypassing those farther south; a few winter in Florida, some in Caribbean, perhaps some in Central America, most in southern South America (Palmer 1988). Breeders from central Alaska migrated through central North America and wintered in southern Mexico, Central America, the Caribbean region, and South America (Britten et al. 1995). Two breeders from southern Utah migrated through western Mexico, and one continued to a wintering site in Nicaragua (Britten et al. 1995). <br /><br />In the U.S., the Atlantic coast from New Jersey to South Carolina and the barrier islands of the Texas Gulf Coast are important feeding areas for long-distance migrants. <br /><br />Arrives in northern breeding areas late April-early May; departure begins late August-early September (Johnson and Herter 1989). See Palmer (1988) for further information on timing of migration. <br /><br />From Padre Island, Texas, a northbound migrant reached south-central Canada in four days, and a southbound migrant passed through Mexico and reached Guatemala in six days (Chavez-Ramirez et al. 1994).","foodHabitsComments":"Feeds primarily on birds (medium-size passerines up to small waterfowl); rarely or locally, small mammals (e.g., bats, lemmings), lizards, fishes, and insects (by young birds) may be taken. Prey pursuit initiated from perch or while soaring. May hunt up to several km from nest site (Skaggs et al. 1988). See Rosenfield et al. (1995) for information on food habits in Greenland.","animalPhenologyComments":"In general, much hunting occurs in morning, and to lesser extent toward evening, but may hunt anytime during day.","colonialBreeder":false,"length":51,"width":null,"weight":1500,"animalPhenologies":[{"animalCagPhenologyId":101963,"animalPhenology":{"id":3,"animalPhenologyDescEn":"Diurnal","animalPhenologyDescEs":"Diurno","animalPhenologyDescFr":"Diurne","displayOrder":3},"adult":true,"immature":true}],"animalFoodHabits":[{"animalCagFoodHabitsId":103651,"foodHabits":{"id":1,"foodHabitsDescEn":"Carnivore","foodHabitsDescEs":"Carnívoro","foodHabitsDescFr":"Carnivore","displayOrder":1},"adult":true,"immature":true}]},"occurrenceDelineations":[{"eoSpecsDetailId":1450,"locationUseClass":{"id":2,"locationUseClassDescEn":"Breeding","locationUseClassDescEs":"En reproducción","locationUseClassDescFr":"Reproduction","displayOrder":2},"eoSpecGroupName":"Peregrine Falcon","subtypes":"Foraging Area, Nest Site","inferredExtentDistance":8.0,"inferredExtentNotes":"Average foraging distance from nest (Brown and Amadon 1968).","minimumEoCriteria":"Evidence of breeding (including historical); and potential 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":"If foraging area is known, it can be mapped in the same EO as a separate source feature from the nest site. Note that foraging areas of different occurrences may overlap.","separationBarriers":null,"separationDistanceUnsuitableHabitatat":20.0,"separationDistanceSuitableHabitatat":20.0,"altSeparationProcedure":null,"separationJustification":"Separation distance is arbitrary. Occurrences represent relatively distinct clusters of one or more nest sites and do not necessarily represent demographically distinct populations. Occurrence separation is based on nest sites; nest sites separated by a gap smaller than the separation distance represent the same occurrence. <br /><br />Foraging ranges up to 27 kilometers radius (Martin 1979), average home range radius about 8-12 kilometers (Brown and Amadon 1968, Porter and White 1973).","versionDate":"2004-09-24","versionAuthor":"Cannings, S., and G. Hammerson","versionNotes":null,"lastModified":"2020-04-30T02:15:14.560562Z"},{"eoSpecsDetailId":1451,"locationUseClass":{"id":3,"locationUseClassDescEn":"Nonbreeding","locationUseClassDescEs":"No reproducción","locationUseClassDescFr":"Non-reproduction","displayOrder":3},"eoSpecGroupName":"Peregrine Falcon","subtypes":"Roost site","inferredExtentDistance":null,"inferredExtentNotes":null,"minimumEoCriteria":"Evidence of recurring presence of wintering individuals outside their breeding area (including historical); and potential recurring presence at a given location. Occurrences should be areas where more than one individual 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":null,"separationDistanceUnsuitableHabitatat":15.0,"separationDistanceSuitableHabitatat":15.0,"altSeparationProcedure":null,"separationJustification":"Separation distance somewhat arbitrary; nonbreeding occurrences based primarily on concentrations of wintering individuals, rather than on distinct populations.","versionDate":"2002-04-16","versionAuthor":"Cannings, S.","versionNotes":null,"lastModified":"2020-04-30T02:15:14.560562Z"}],"plantCharacteristics":null,"elementManagement":{"elementGlobalId":102654,"eoManagementGroupName":null,"stewardshipOverview":null,"impacts":null,"restorationPotential":null,"siteConservationPlansConsidered":null,"managementMethods":"Potholes dug into cliffs are readily accepted as nest sites in some areas. <br><br>Reintroduction using captive-raised birds (thousands have been released) has been partially successful, more so in the U.S. than in Canada (Peakall 1990). See Holroyd and Banasch (1990) for summary of results of reintroductions in southern Canada and recommendations to improve future release efforts. See Sherrod et al. (1982) for information on reintroduction methods. See The Peregrine Fund (1992) for a recent summary of release data. See also Cade et al. (1988). <br><br>See Skaggs et al. (1988) and Lefranc and Glinski (1988) for management recommendations for the southwestern U.S. <br><br>See Johnson (1988) for responses to various human stimuli at different distances from nesting areas.","monitoringMethods":"See Britten et al. 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