Anser erythropus 

Scope: Global
Language: English

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Taxonomy [top]

Kingdom Phylum Class Order Family
Animalia Chordata Aves Anseriformes Anatidae

Scientific Name: Anser erythropus
Regional Assessments:
Common Name(s):
English Lesser White-fronted Goose
Identification information: 53-66 cm. Small, grey-brown goose. White patch at base of pink bill. Black belly patches. Yellow eye-ring at close range. Similar spp. White-fronted Goose A. albifrons larger, longer necked with bigger bill and less steeply sloping forehead. Adult less dark and has smaller white blaze on face and lack bright yellow eye-ring. Juvenile lacks pale eye-ring. Difficult to distinguish in flight except by longer neck and bill and relatively shorter wings. Voice Fast bouncing dyee yik. Hints Search flocks of other geese, particularly A. albifrons. Walks faster than A. albifrons and is consequently often found near the front of feeding flocks.

Assessment Information [top]

Red List Category & Criteria: Vulnerable A2bcd+3bcd+4bcd ver 3.1
Year Published: 2017
Date Assessed: 2016-10-01
Assessor(s): BirdLife International
Reviewer(s): Butchart, S. & Symes, A.
Contributor(s): Morozov, V., Petkov, N., Zöckler, S., Scott, A.D., Mikander, N., Øien, I., Aarvak, T., Ikeuchi, T., Fox, A., Bräunlich, A. & Vougioukalou, M.
Facilitator/Compiler(s): Benstead, P., Derhé, M., Jones, V., Malpas, L., Pilgrim, J., Symes, A., Westrip, J.
This species is listed as Vulnerable because it has suffered a rapid population reduction in its key breeding populations in Russia, and equivalent declines are predicted to continue. The Fennoscandian population has undergone a severe historical decline, and has not yet recovered.

Previously published Red List assessments:

Geographic Range [top]

Range Description:Four subpopulations of Anser erythropus can be recognised - three of which are surviving components of the species’ formerly extensive breeding range: the Fennoscandian population which breeds in the Nordic countries (Norway 20-25 pairs, Finland 0-5 pairs, Sweden 15-25 pairs (which has been reinforced by reintroductions) [BirdLife International 2015]) and the Kola Peninsula in Russia; the Western Asian main population which breeds in northern Russian tundra to the centre of the Taimyr Peninsula, including Putorana Plateau, and to the west and east of Pechora and Western Siberia (Yamal and Gydan peninsulas); and the Eastern Asian main population which breeds in the southern Taimyr and areas north of Eastern Siberia and Chukotka. Fennoscandian breeders overwinter at Kerkini Lake and in the Evros Delta between Greece and Turkey (Lorentsen et al. 1998). A small wintering population is also now established in The Netherlands, which originates from the reintroduced breeding population in Sweden. Birds from the Western Asian main population winter around the Black and Caspian Seas, mainly in Azerbaijan, Iraq, Iran and Uzbekistan (V. Morozov in litt. 2016, N. Mikander, I. Øien and T. Aarvak in litt. 2016); and birds from the Eastern Asian main population winter in the Yangtze River Valley in China (following considerable range contractions in this country [A. Fox in litt. 2016]), the Korean Peninsula and in Japan (N. Mikander in litt. 2016). Fennoscandian breeding birds occur on passage mainly in Finland, Estonia and Hungary, while many non-breeders migrate through Russia and Kazakhstan (Tolvanen et al. 1999, Morozov and Syroechkovski 2005, Aarvak and Øien 2003), and in smaller numbers in Lithuania, Slovakia, Romania (Aarvak et al. 1997; Munteanu et al. 1991) Bosnia and Herzegovina, Albania, and Bulgaria (Petkov et al. 1999). Birds from the Western Asian main population occur during passage mainly in Kazakhstan, but also Syria, Turkmenistan, Ukraine, and Uzbekistan (Jones et al. 2008); and birds from the Eastern Asian main population possibly stop-over in Mongolia (A. Bräunlich in litt. 2011, N. Mikander in litt. 2016). Due to limited genetic introgression of Greater White-fronted Goose genetic material in the reinforced Swedish population, some concerns have been raised about whether that population should be considered in the current Red List assessment. The current Guidelines for Using the IUCN Red List Categories and Criteria (Version 11, February 2014) do not provide any guidance on what levels of hybrid gene frequency are acceptable to allow inclusion of populations of released birds from captive breeding programmes in a Red List assessment. However, a global assessment of Red List Category is not affected by this debate.

The most recent total population estimate is 24,000-40,000 individuals, which compares with previous published global estimates of 25,000 to 30,000 individuals (Lorentsen et al. 1999) and 22,000 to 27,000 (Delany & Scott 2006). This includes 10,000-21,000 individuals in autumn in its Western Palearctic range (Jones et al. 2008, Fox et al. 2010) and 14,000-19,000 individuals from the East Asian Flyway (Jia et al. 2016, C. Lei per A. Fox in litt. 2016) (64,000 in 1988-1993 [Jia et al. 2016]; 20,000 recorded in 1997 [Li and Mundkur 2004]; but later less than 17,000 (Morozov and Syroechkovski 2005); 16,937 counted in Lower Yangtze Valley in 2004 (Barter et al. 2004), and 16,600 counted in East Dongting Lake nature reserve in 2004 [Barter 2005]). The Russian populations have declined from a former estimate of 30,000-50,000 individuals (Morozov 1995). The Fennoscandian population has declined from more than 10,000 birds in the early 20th century.

Countries occurrence:
Armenia; Azerbaijan; Belarus; Bosnia and Herzegovina; Bulgaria; China; Croatia; Estonia; Finland; Georgia; Germany; Greece; Hungary; Iran, Islamic Republic of; Iraq; Japan; Kazakhstan; Korea, Democratic People's Republic of; Korea, Republic of; Latvia; Lithuania; Macedonia, the former Yugoslav Republic of; Moldova; Mongolia; Montenegro; Norway; Poland; Romania; Russian Federation (Central Asian Russia, Eastern Asian Russia, European Russia); Serbia; Slovakia; Sweden; Syrian Arab Republic; Tajikistan; Turkey; Turkmenistan; Ukraine; Uzbekistan
Afghanistan; Albania; Austria; Belgium; Czech Republic; Denmark; Egypt; France; India; Ireland; Israel; Jordan; Myanmar; Oman; Pakistan; Spain; Switzerland; Taiwan, Province of China; United Arab Emirates; United Kingdom; United States
Additional data:
Continuing decline in area of occupancy (AOO):Yes
Extreme fluctuations in area of occupancy (AOO):NoEstimated extent of occurrence (EOO) - km2:7060000
Continuing decline in extent of occurrence (EOO):YesExtreme fluctuations in extent of occurrence (EOO):No
Number of Locations:11-100Continuing decline in number of locations:Unknown
Extreme fluctuations in the number of locations:No
Upper elevation limit (metres):700
Range Map:Click here to open the map viewer and explore range.

Population [top]

Population:In its Western Palearctic range the population has been estimated at 10,000-21,000 individuals in autumn (Jones et al. 2008, Fox et al. 2010); and the East Asian Flyway estimates are 14,000-19,000 individuals (Jia et al. 2016, C. Lei per A. Fox in litt. 2016). This gives a global population estimate of 24,000-40,000 individuals, roughly equivalent to 16,000-26,666 mature individuals, rounded here to 16,000-27,000 mature individuals.

Trend Justification:  This species' population is suspected to have decreased rapidly, owing to levels of hunting on the staging and wintering grounds, and habitat deterioration (largely as a result of land cultivation). The decrease in numbers has been accompanied by fragmentation of the breeding range and is continuing to affect all populations. Modelling indicates that 28% of the habitat for this species could be lost by 2070 (Zöckler and Lysenko 2000).
Current Population Trend:Decreasing
Additional data:
Number of mature individuals:16000-27000Continuing decline of mature individuals:Yes
Extreme fluctuations:NoPopulation severely fragmented:No
No. of subpopulations:2-100Continuing decline in subpopulations:Unknown
Extreme fluctuations in subpopulations:NoAll individuals in one subpopulation:No
No. of individuals in largest subpopulation:1-89

Habitat and Ecology [top]

Habitat and Ecology:Behaviour This species is fully migratory, and information about its migration routes has only recently come to light as a result of satellite telemetry studies and increased monitoring efforts (Lorentsen et al. 1998, Aarvak and Øien 2003, Kear 2005a). The species departs from its breeding grounds in northern Scandinavia and Arctic Russia in late August to early September. The Fennoscandian population follows several routes: either south (through Hungary), or east and then south, through the Russian Taimyr Peninsula in northern Siberia, northern Kazakhstan and finally the Black Sea (Snow and Perrins 1998, Øien et al. 2005), to reach wintering grounds in south-east Europe. The West Asian main population migrates mainly south along the Ob River Valley in Russia, via the same staging grounds in northern Kazakhstan to wintering grounds in Azerbaijan and the Middle East (around the Caspian Sea and the Persian Gulf) (Snow and Perrins 1998, Alerstam 1990). The East Asian main population winters in eastern China (del Hoyo et al 1992) and the Korean peninsula (Madsen 1996) as well as increasingly in Japan (some 100 individuals [Toshio Ikeuchi per N. Mikander in litt. 2016]). The return passage to the breeding grounds begins in February, with the species arriving from early May (Snow and Perrins 1998) to late June (Madsen 1996). In Siberia non-breeding birds undertake a moult-migration to higher altitudes or to areas north of the breeding range (Madsen 1996) and non-breeders or failed breeders from the Fennoscandian population migrate eastwards and join these flocks before the onset of moulting (Aarvak and Øien 2003). Evidence indicates that this species is not a colonial breeder (Johnsgard 1978), but nests in pairs on isolated territories (Madge and Burn 1988). However, the species is gregarious outside the breeding season (Madge and Burn 1988). Habitat Breeding This species breeds in low-lying bogs, scrub-covered tundra and taiga-forest edges close to wetlands, up to 700 m above sea level (Kear 2005a). It can also be found on the slopes by lower parts of mountain streams, on mountain foothills, mountain lakes and on alpine precipices, often in thawing boggy areas or on stonefields (Johnsgard 1978; Cramp and Simmons 1977). Adults of this species undergo a post-breeding flightless summer moult whilst still in their breeding range (in Siberia and Fennoscandia non-breeding adults migrate to areas north (West Asian main) or east (Fennoscandian) of the breeding range or to higher altitudes to exploit large open water fringed with sedge (Carex), or river valleys with long grass and scrub to escape predation) (Aarvak and Øien 2003, Kear 2005a). Non-breeding During winter and on migration this species frequents open short grassland in the steppe and semi-arid zones, particularly in sodic (e.g. seashore) pastures, arable farmland, pastures and meadows (Madsen 1996; Kear 2005a; Cramp and Simmons 1977). Winter roosting colonies are also formed on large lakes and rivers (Madge and Burn 1988; Cramp and Simmons 1977), or in reedbeds and rushes (Cramp and Simmons 1977). Diet This species is herbivorous, feeding on grasses, roots, stems, leaves, fruits and the green parts of aquatic and terrestrial plants along lake-shores, rivers and marshes (Kear 2005a). During the winter the species supplements its diet with winter agricultural grains (Kear 2005a). Breeding site Birds of this species often nest on snow-free patches available early in the breeding season (such as rocky outcrops or prominent hummocks) hidden amongst vegetation (grass, dwarf shrub heathland) or in boggy hollows (Madsen 1996; Kear 2005a), usually in close proximity to open water or marshy areas (Kear 2005a).

Systems:Terrestrial; Freshwater
Continuing decline in area, extent and/or quality of habitat:Yes
Generation Length (years):11.4
Movement patterns:Full Migrant
Congregatory:Congregatory (and dispersive)

Threats [top]

Major Threat(s): Disturbance on breeding grounds (e.g. from increasing tourism, angling and reindeer husbandry) causes much disruption to nesting birds in Fennoscandia (Madsen 1996, N. Mikander in litt. 2016) and disturbance by hunters can be a significant limiting factor on survival and breeding output (Ebbinge and Spaans 1995; Ä 2000; N. Petkov in litt. 2007). Illegal spring hunting and round-ups of moulting birds are taking place on the Russian breeding grounds (Jones in press) and illegal shooting continues in Norway (T. Aarvak pers. comm. 2007). In autumn and winter, illegal killing (including by poisoning [A. Fox in litt. 2016]) and accidental shooting on the staging and wintering grounds is the most important threat (Madsen 1996; Aarvak et al.1997; Lorentsen et al. 1998; Kear 2005a; Morozov 2006; Jones [in press]). In the Western Palearctic at least 20-30% of the population are shot each year (Mooij 2010) often accidentally during hunting of other species. Habitat deterioration, as a result of land cultivation and increased water-levels in the Caspian Sea, is a further threat (Madsen 1996), as is habitat loss through the creation of reservoirs for hydroelectric power in Scandinavia (Madsen 1996). The species may also be threatened by nest predation from the Red Fox Vulpes vulpes and Arctic Fox Alopex lagopus (Madsen 1996, V. Morozov in litt. 2016). Climate change and associated habitat shifts are expected to impact negatively on this species and others dependent on tundra habitat for breeding. Modelling indicates that 28% of the habitat for this species could be lost by 2070 (Zöckler and Lysenko 2000). The wintering population at Dongting Lake, China, is considered to now be relatively stable, but the concentration of the majority of birds in this population at one site makes it extremely vulnerable to any factor that could affect this locality (Cong et al. 2012), most notably with changing hydrology and water quality of the Yangtze River (A. Fox in litt. 2016). This is especially the case because the species is reliant on specialist recessional grasslands in spring and autumn (Wang et al. 2012, 2013). In the Kaliningrad region of Russia, important migratory stop-over points on the Baltic Sea coastline are being degraded through petroleum pollution, wetland drainage for agriculture, changes in wetland management leading to scrub and reed overgrowth, peat extraction, and the burning and mowing of reed beds (Grishanov 2006).

Conservation Actions [top]

Conservation Actions: Conservation Actions Underway
CMS Appendix I and II and designated for Concerted Action (CMS Resolution 5.1). Listed in Table 1 Column A of the Action Plan under the African-Eurasian Migratory Waterbird Agreement (AEWA) and in Annex II ‘Strictly protected species’ of the Bern Convention. Listed in Annex 1 of the EU Birds Directive. It is protected in most of its key range states.  An European Action Plan was published in 1996 (Madsen 1996) and an updated International Single Species Action Plan for the western Palearctic population was published in 2008 (Jones et al. 2008). Inter-governmental AEWA Lesser White-fronted Goose (LWfg) International Working Group was convened in 2009 to guide and lead on international conservation efforts for the species under the framework of the International Action Plan. Cooperation between various NGOs and national governments and other stakeholders further supports the implementation of concrete conservation action along the flyways – particularly for the Fennoscandian population, but increasingly also for the Western main population (N. Mikander in litt. 2016). Discussions are ongoing to develop International Action Plan for Eastern Asian main population in cooperation with East-Asia Australasia Flyway Partnership and Eastern Asian main population range states invited to join the AEWA LWfG International Working Group (N. Mikander in litt. 2016). The species has also been singled out as a priority species in the Arctic Migratory Bird Initiative (AMBI) of the Arctic Council biodiversity working group CAFF (Conservation of Arctic Fauna and Flora) (N. Mikander in litt. 2016). Satellite telemetry studies have improved knowledge of its ecology and the key threats (Aarvak et al.1997; Tolvanen et al. 1999). Several captive breeding populations exist (AEWA), though the reintroduction programme in Sweden recently ended. Public awareness materials have been produced (Kostadinova et al. 1999). The species is monitored under the AEWA LWfG Working Group for the Western Palearctic populations (N. Mikander in litt. 2016), and since 2011 it has been the subject of a LIFE+ project (M. Vougioukalou in litt. 2012).

Conservation Actions Proposed

Work plan adopted under the AEWA LWfG International Working Group for 2016-2019 includes activities to reduce hunting pressure in key wintering and staging areas; locate, monitor and protect key areas; continue satellite tracking and other research; prevent habitat loss and manage habitats in staging and wintering areas; promote the implementation of national legislation; and promote public awareness amongst key stakeholders and communities (N. Mikander in litt. 2016). Possibly develop captive breeding programmes (Collar and Butchart 2013), and promote international legal protection for the species.

Amended [top]

Amended reason: There have been edits to the text of Habitat and Ecology, Geographic Range, Population, Conservation Actions, Rationale and Threats Information. The estimates for number of individuals, mature individuals and mature individuals in the largest subpopulation have been edited, though have not crossed any Red List threshold. Details regarding seasonality and origin in Countries of Occurrence have been edited, as have details regarding International Legislation, Systematic Monitoring Scheme and Action Recovery Plan as part of the Actions in Place. The reference list has subsequently been updated and new Contributors and a new Facilitator/Compiler have been added.

Citation: BirdLife International. 2017. Anser erythropus (amended version of 2016 assessment). The IUCN Red List of Threatened Species 2017: e.T22679886A110188981. . Downloaded on 16 August 2018.
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