Current view: Data table and detailed info
Taxonomic note
Closely related to L. limosa, and elsewhere previously considered conspecific. Monotypic.
Taxonomic source(s)
AERC TAC. 2003. AERC TAC Checklist of bird taxa occurring in Western Palearctic region, 15th Draft. Available at: http://www.aerc.eu/DOCS/Bird_taxa_of_the_WP15.xls.
Christidis, L. and Boles, W.E. 2008. Systematics and Taxonomy of Australian Birds. CSIRO Publishing, Collingwood, Australia.
del Hoyo, J., Collar, N.J., Christie, D.A., Elliott, A. and Fishpool, L.D.C. 2014. HBW and BirdLife International Illustrated Checklist of the Birds of the World. Volume 1: Non-passerines. Lynx Edicions BirdLife International, Barcelona, Spain and Cambridge, UK.
SACC. 2005 and updates. A classification of the bird species of South America. Available at: https://www.museum.lsu.edu/~Remsen/SACCBaseline.htm.
Turbott, E.G. 1990. Checklist of the Birds of New Zealand. Ornithological Society of New Zealand, Wellington.
IUCN Red List criteria met and history
Red List criteria met
Red List history
| Migratory status |
full migrant |
Forest dependency |
does not normally occur in forest |
| Land-mass type |
|
Average mass |
- |
Population justification: The population size is estimated to be 41,000 to 70,000 mature individuals.
Simultaneous surveys of the Atlantic portion of the non-breeding range in January 2019 recorded a mean total of 56,276 (9,326-113,221) individuals, using two step ‘hurdle’ generalised linear models to predict abundance in different habitat classes (Faria et al. in press). The wide confidence intervals are a cause for caution in using this value and the total number of individuals observed in the production of this estimate is only 1,317 (Faria et al. in press), in contrast to the 45,500 individuals counted during aerial surveys in the 1980s (Morrison and Ross 1989). These caveats aside, it is a considerable simultaneous effort to sample the non-breeding range that hosts more than 70% of the population. To account for the large uncertainty in this data this assessment uses the second quartile range of values (25-50%) as a precautionary position. This is considered necessary especially in light of data indicating extremely rapid declines in monitored migration sites in North America (Smith et al. 2023). The lower bound of the second quartile is 28,959 individuals, hence a cautious range is given for this estimate of 29,000-56,300 individuals. Faria et al. (in press) did not estimate numbers for Chilean sites, hence it appears the birds occurring at Bahia Lomas in Chile (Morrison unpublished data, in COSEWIC 2019, Morrison and Ross 1989) are not included in these counts. Hence the c. 18,000 individuals counted at this site in 2018 (Morrison unpublished data, in COSEWIC 2019) need adding to this estimate, increasing it to 47,000-74,300 individuals. There have been subsequent aerial counts of the Bahia Lomas non-breeding population: 20.423 ± 639 individuals in January 2022 (Norambuena et al. 2022b) and 24,038 ± 148 individuals in January 2023 (Norambuena et al. 2023): but the proximity of the site to those covered by Faria et al. (in press) suggests that the precautionary position is to use the values closest in time in case of interannual dispersal between non-breeding sites.
Almost all the remaining non-breeding birds occur around Chiloe Island on the Pacific coast of Chile (Morrison and Ross 1989, Espinosa et al. 2005, Andres et al. 2009, García Walther 2016, Fink et al. 2023, Walker et al. 2024). This has most recently been estimated at 18,640 individuals (excluding potentially inflationary extrapolation to non-surveyed sites) from surveys in 2014 (García Walther 2016). This latter total is comparable in method to the 20,961 individuals reported by Andres et al. (2009) for 2007-8, and the 21,282 individuals in 1997 (Espinosa et al. 2005).Summing the most recent values for the two regions gives a range of 65,599 – 92,916 individuals, rounded to 65,600-93,000 for the region that hosts nearly all non-breeding birds. While small numbers are present further north as far as Piura, Peru (Senner 2008, Fink et al. 2023), these are not thought to add significantly to this estimate.The median value is very similar to the 77,000 individuals given by Andres et al. (2012), which was based on an earlier estimate of 56,000 individuals for the Tierra del Fuego (and Samborombon Bay) non-breeding population (Morrison et al. 2006) plus 21,000 individuals for the Chiloe population (Andres et al. 2009).These estimates, all based on non-breeding counts, include immature birds. Assuming these represent between one quarter (COSEWIC 2019) and one third of the counted individuals then the population size falls between 43,000 and 70,000 mature individuals.
Much of the above data was used in the COSIEWIC assessment of Hudsonian Godwit in 2019 (COSEWIC 2019), which gave a revised population estimate of 41,000 mature individuals. This differed in using a lower estimate for the Tierra del Fuego wintering population of 32,400 ± 5,900 based on the average count over 2011-2018 (Morrison unpublished data, in COSEWIC 2019) plus a separate estimate for Samborombon Bay in Argentina of 1,070 ± 290 individuals (Martínez-Curci and Isacch 2017). Averaged count values can be underestimates for a target species that can switch sites between years, often leading to apparent large fluctuations in numbers at small geographic scales: this was noted for counts in the Chiloe region by Espinosa et al. (2005). But this lower value (based on count data rather than modelled abundance) is comparable with the lower quartile value used as a precautionary bound above. The counter suggestion is that a modelling method can perform poorly for species that aggregate in large flocks, hence occur only patchily across apparently suitable habitat. This is certainly the case for this species. Given that the estimate falls so close to the lower bound of that derived from the above approach, this estimate is accepted as the lower bound of the population size.
A separate population estimate of 70,710 ± 30,385 individuals was derived from 2002-2003 spring migration counts in the U.S. Prairie Pothole region (Skagen et al. 2008). It is assumed that almost all godwits heading to the breeding grounds (a proportion remain in non-breeding areas [Navedo and Ruiz 2020]) are mature individuals. It is notable that this value is comparable to that derived from the non-breeding data. The value of 7 days for stopover duration used was a generic value based on a small number of observations relating to other species of shorebird (Skagen et al. 2008). Morrison et al. (2006) considered a conservative approach assuming the true value lies within 1 SE below the mean, which gives an estimate from this data of 40,300-70,700 mature individuals.
This is a wholly migratory species for which there do not appear to be any barriers to dispersal, and there is no known variation in morphology. Despite this, significant genetic divergence was reported between the Hudson Bay and Mackenzie Delta breeding individuals, though based on a sample of only 20 individuals (Haig et al. 1997). It appears there is also some evidence of migratory connectivity of Alaskan breeding birds and wintering areas on the Pacific coast of Chile, and separately the remaining breeding population wintering on the Atlantic coast and Tierra del Fuego (Senner 2010). However, tracking data has shown that individuals may move between these areas prior to northbound migration (COSEWIC 2019, Walker et al. 2024) and it is considered most likely that there is regular individual dispersal between different breeding areas. If the Alaska/Pacific population is a separate subpopulation, the current estimate of the population size is 12,300 mature individuals (García Walther 2016), which would be 30% of the minimum population size.
Trend justification: Somewhat contradictory data makes assessment of the current trend uncertain, despite considerable monitoring effort. Recent non-breeding estimates suggests the population has been largely stable, but uncertainty in this data may obscure the true trend. All other data indicates declines.
A moderately rapid to rapid rate of decline is weakly suggested from the repeated counts between 1997 and 2014 from the Pacific coast of Chile. Using the values given in the population size text from Espinosa et al. (2005), Andres et al. (2009) and García Walther (2016) (see above) the reduction in this region is equivalent to -21% (-14 to -28%) over three generations: this rate appears to be accelerating however updated counts are needed.
Median values from the most recent estimate of the Atlantic non-breeding population (most of the global population) suggest long-term stability (Faria et al. in press), which would bring the total rate of reduction to below 6% over three generations. However, recorded declines in the counts at the two single most important sites in Tierra del Fuego of -4.08% (95% CI of -6.19 to -2.14) annually between 2002 and 2018 (Morrison unpublished data, in COSEWIC 2019) suggest there could be a rapid reduction taking place. Using the most recent lower estimate from the count data for the Atlantic non-breeding population (Morrison unpublished data, in COSEWIC 2019), plus 1,070 individuals for Samborombon Bay and combined with the Pacific coast values gives a rapid overall three-generation reduction of 37% (the value of 44% given in COSEWIC [2019] fails to recalculate relative proportions of the total population with the decline).
A separate rate can be obtained from the range of uncertainty given for the recent Atlantic coast non-breeding estimate (Faria et al. in press). Using the lower quartile value from Faria et al. (in press) of 28,959 individuals in 2019, plus the value of 18,000 for Bahia Lomas (see population size section) gives 46,859, equivalent to a 17% reduction over three generations from the 2000 estimate of 56,000 (Morrison et al. 2006). When combined with the values for the Pacific population this gives an overall reduction of 20 % over the past three generations. Recent slightly increased numbers counted at Bahia Lomas (Norembuena et al. 2022, 2023, Centro Bahía Lomas of the Universidad Santo Tomás/Red de Observadores de Aves y Vida Silvestre de Chile [ROC] in litt. 2024) may suggest a lower overall rate of reduction, or may reflect the redistribution of individuals between wintering sites in different years.
This still contrasts starkly with the migration count data (Smith et al. 2023) which estimates a population reduction equivalent to 88.4% (-95.1 to -73.4%) over three generations. These data are also used in the Avian Conservation Assessment Database December 2023 update (Partners in Flight 2023). The contradiction may be because only a small proportion of the population are thought to be available to sample through the migration sites monitored (COSEWIC 2019, ECCC 2019). Most individuals make a non-stop flight to South America and skip the migration survey sites (Morrison 1984, Walker et al. 2024). But there has clearly been an extremely rapid reduction in the number of individuals available to be recorded within this extensive network of sites biased to the eastern half of North America (COSEWIC 2019). While this may partly be explained by a shift in migratory behaviour, there is evidence for moderately rapid to rapid declines in the non-breeding season data, although the true rate of these declines is unlikely to match those reported by Smith et al. (2023).
Overall, a population reduction of between -20 and -37% is suspected to have taken place over the past three generations, and this rate of reduction is inferred to be continuing over the three generations that span 2011 and 2032.
Country/territory distribution
Important Bird and Biodiversity Areas (IBA)
Recommended citation
BirdLife International (2024) Species factsheet: Hudsonian Godwit Limosa haemastica. Downloaded from
https://datazone.birdlife.org/species/factsheet/hudsonian-godwit-limosa-haemastica on 23/12/2024.
Recommended citation for factsheets for more than one species: BirdLife International (2024) IUCN Red List for birds. Downloaded from
https://datazone.birdlife.org/species/search on 23/12/2024.
