|Scientific Name:||Brachyramphus marmoratus|
|Species Authority:||(Gmelin, 1789)|
|Taxonomic Source(s):||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.|
|Identification information:||25 cm. Chunky alcid. Breeding plumage is dark brown above, heavily mottled below. In winter, dark grey above and white below with white scapulars, dark marks on side of breast, dark ear-coverts and whitish eye-ring. Juvenile resembles winter adult but darker scapulars and dusky mottling below. Similar spp Kittlitz's Murrelet B. brevirostris is paler, has white outer tail feathers and shorter bill. In winter, has whiter face broken by dark eye and slight eye-stripe, nearly complete breast-band and white tips to secondaries.|
|Red List Category & Criteria:||Endangered A2bc+3bc+4bc ver 3.1|
|Reviewer(s):||Butchart, S. & Symes, A.|
|Contributor(s):||Bertram, D., Burger, A.E., Kuletz, K., Nelson, K. & Piatt, J.|
|Facilitator/Compiler(s):||Benstead, P., Calvert, R., Derhé, M., Gilroy, J., Moreno, R.|
This species is still abundant, but it is treated as Endangered because its population is estimated to have undergone a very rapid reduction, especially in the southern portion of its range, which is expected to continue, owing to a variety of threats.
|Previously published Red List assessments:|
Brachyramphus marmoratus occurs in the USA and Canada in California, Oregon, Washington, British Columbia, south-east Alaska, Prince William Sound, Kenai Peninsula, Lower Cook Inlet, Barren Islands, Afognak and Kodiak Islands, the Alaska Peninsula and the Aleutians locally to Andreanof and Near Islands (Gaston and Jones 1998). In Alaska (70% of the population), historical estimates place the population at c. 750,000 individuals, though when trend estimates are applied to this figure it gives an estimated 2006 population of c. 271,000 individuals (Piatt et al. 2007). The British Columbia population was previously thought to be c. 54,000 - 92,500 (Piatt et al. 2006) but extrapolations from recent radar counts suggest the population may in fact be c. 72,600-125,600 birds (COSEWIC 2012). This higher estimate is likely due to differences in survey methodology as opposed to a genuine population increase. The population in Washington, Oregon and California is estimated at 15,400-23,900 individuals (Falxa et al. 2014, Falxa and Raphael 2016). The greatest historical decreases have occurred in Washington, Oregon and California, and these continue (A. Burger in litt. 2012, Falxa et al. 2016). Declines are also reported in British Columbia and south-east Alaska (Perry 1995). Trend analyses conducted during 2000-2013 suggests a decline of c.11% over the period in Washington, Oregon and California (Falxa et al. 2014, Falxa and Raphael 2016), and a decrease of c.70% in Alaska from the 1980s to 2006 (Piatt et al. 2006). At-sea surveys over the past 25 years in British Columbia suggest declines of c.1% per year (Piatt et al. 2006) although radar surveys suggest the population may have been relatively stable since 1999 with declines in some regions of British Columbia (COSEWIC 2012, Bertram et al. 2015). Availability of nesting habitat in British Columbia, which is strongly correlated with local breeding populations (Burger 2001, Burger et al. 2004), has declined by 22% between 1978 and 2008, and is continuing (COSEWIC 2012).
Native:Canada; United States
|Range Map:||Click here to open the map viewer and explore range.|
COSEWIC (2012) estimated the total population to number 358,200-417,500 individuals, rounded here to 350,000-420,000 individuals, based on 271,000 individuals in Alaska (Piatt et al. 2007), 72,600-125,600 in British Columbia (Bertram et al. 2007), and 15,400-23,900 individuals in Washington, Oregon and California (Falxa et al. 2014).
Trend Justification: The population was estimated to have declined by c.11% in 2000-2013 in Washington, Oregon, and California (Falxa et al. 2014), with a 50% decrease in Alaska in 1972-1992 (Piatt and Naslund 1995). At-sea surveys over the past 25 years in British Columbia suggest declines of c.1% per year (Piatt et al. 2006) although radar surveys suggest the population may have been relatively stable since 1999 with declines in some regions of British Columbia (COSEWIC 2012, Bertram et al. 2015). Availability of nesting habitat in British Columbia, which is strongly correlated with local breeding populations (Burger 2001, Burger et al. 2004), has declined by 22% between 1978 and 2008, and is continuing (COSEWIC 2012). Declines are suspected to be very rapid and on-going due to very low measured productivity rates.
|Current Population Trend:||Decreasing|
|Habitat and Ecology:|
It nests in old-growth and older-aged trees (up to 60 km inland) and on the ground (only in northerm part of range) (Piatt and Ford 1993, Ralph 1995, Gaston and Jones 1998, Burger 2002, McShane et al. 2004, Piatt et al. 2006, Barbaree et al. 2014), with the breeding season stretching between March and September in California, April and September in British Columbia, and May and September in Alaska (Piatt et al. 2006). Forest areas with multiple canopy layers and high moss abundance are strongly preferred. Research in British Columbia shows that in areas where forest habitat is relatively plentiful the species seldom re-use the same trees as nest sites, whereas in areas where logging has reduced old-growth there is a higher proportion of nest tree re-use (Burger et al. 2009). The species has been shown to suffer increased predation and disturbance at forest edges adjacent to recently cleared areas, compared with forest edges adjacent to regenerating or riparian areas (Malt and Lank 2007, 2009). Multiple radar and modelling studies have shown a significant correlation between numbers of birds entering watersheds and the areas of suitable forest habitat within those watersheds (Burger 2002, Burger et al. 2004, Raphael et al. 2011). Breeding is mid-March to early September in California, but more compressed further north (Hamer and Nelson 1995a, 1995b, Gaston and Jones 1998, Burger 2002). The diet is sandlance, herring, other small schooling fish and, in winter, invertebrates (Gaston and Jones 1998, Piatt et al. 2006). Chicks are generally fed large subadult or adult prey rather than juveniles or larvae (Piatt et al. 2006). It feeds in near-shore habitats up to 1.4 km offshore, in sheltered waters, lagoons and sometimes inland lakes (Carter 1986, Hunt 1995, Gaston and Jones 1998, Burger 2002, Hebert and Golightly 2008). The affect of marine attributes on murrelet productivity varies from increasing density and productivity estimates with increasing sea surface temperature in the San Juan Archipelago, Washington (1995-2007; Raphael and Bloxton 2008), to decreasing reproductive efforts with warmer sea-surface temperatures in California (Bigger and Chinnici 2008). Sea-surface temperatures and other marine attributes explained little of the variation in murrelet distribution and abundance compared to the amount and cohesion of forest nesting habitat (Raphael et al. 2015). Daily movements to feeding areas can be up to 250 km in exceptional cases (Whitworth et al. 2000) but are normally about 30 km (Burger 2002, Piatt et al. 2006). Radio-marked birds from Redwood Creek in North California moved a maximum average distance of 99 km alongshore, with males travelling further than females, and non-breeding males travelling further than breeding males perhaps in search of mates or nesting habitats. Average home range size was 505 km2, again being greater for males than females (Hebert and Golightly 2008). Individuals exhibit plasticity in their foraging behaviour, foraging closer to shore and increasing dive rates during nesting (Peery et al. 2009). Marbled Murrelets most often forage in pairs (Piatt et al. 2006). Individuals in the northern part of its range may travel south during the non-breeding season, a movement which likely reflects the availability of prey (Piatt et al. 2006).
|Systems:||Terrestrial; Freshwater; Marine|
|Continuing decline in area, extent and/or quality of habitat:||Yes|
|Generation Length (years):||10|
|Movement patterns:||Not a Migrant|
|Congregatory:||Congregatory (and dispersive)|
Many areas of remaining old-growth and older-aged forest used as nesting habitat are slated for logging, especially on private, state or provincial lands. Loss of nesting habitat is strongly linked with declining populations through most of the species range (Burger 2002, Burger and Waterhouse 2009, Piatt et al. 2006). Multiple radar studies have shown that when breeding habitat is reduced by logging, the birds do not simply relocate to remaining forest patches in higher densities, but suffer a population decline (Burger 2001, Burger et al. 2004, Raphael et al. 2006). This strongly suggests that population declines through much of its range have been driven, at least in part, by loss of nesting habitat (Burger 2002). Murrelet distribution and abundance is directly correlated to the amount and cohesion of forest nesting habitat (Raphael et al. 2015). The species has been found to suffer increased corvid predation and disturbance at forest edges adjacent to recently cleared areas (Burger 2002, Malt and Lank 2007, 2009). Juvenile recruitment off Vancouver Island was significantly reduced in a year of low marine productivity and prey availability (Ronconi and Burger 2008). Since the collapse of the Pacific sardine fishery, prey quality and abundance has declined, with lower trophic-level prey (e.g. krill) now dominating the pre-breeding diet in California (Becker and Bessinger 2006). This has resulted in a lower proportion of individuals reaching breeding condition, and therefore lower population productivity. This factor, combined with high rates of nest predation by corvids and continued loss of habitat, is thought to be the primary cause of recent declines and sustained low recruitment in Washington, Oregon and California (Peery et al. 2004, USFWS 2012). Nylon, monofilament gill-nets in shallow waters and oil-spills (e.g. Exxon Valdez, Nestucca and New Carissa) also cause considerable mortality (Piatt and Naslund 1995, Nelson 1997, Gaston and Jones 1998, Burger 2002, Titmus and Smith 2008). A 2010 study suggests genetic divergence of the species in central California, despite c.7% of this population being classified as migrants, as individuals dispersing from northern populations contribute relatively few young to the central California population (Peery et al. 2010).
Conservation Actions Underway
The U.S. Department of Natural Resources (WDNR) began developing a Marbled Murrelet Long-Term Conservation Strategy in 2007 (Escene 2007); the final strategy still has not been released as of 2016. The Northwest Forest Plan (1994) is expected to ensure the protection of a large proportion of important habitats in the USA (Raphael 2006).
Extensive areas of suitable forest nesting habitat have been set aside in conservancies on the northern and central mainland and in Haida Gwaii (formerly Queen Charlotte Islands) (COSEWIC 2012). Smaller areas are being protected by other forestry and conservation measures. Overall, an estimated 35% of the 1,826,828 hectares of suitable habitat in all of British Columbia (based on the Canadian Marbled Murrelet Recovery Team modeling criteria [CMMRT 2003]) had been protected under various measures by 2011 (COSEWIC 2012). In 1998, the Exxon Valdez Trustee Council protected 179 km2 of Afognak Island (BBC Wildlife 1999 172: 23). In 2007, 1,569 ha of forested land on the Oregon Coast was acquired under conservation easement for the species (amongst others), part funded by the New Carissa oil-spill funds (Escene 2007). Between 1998 and 2002, 507 Marbled Murrelets were radio-tracked in British Columbia (Zharikov et al. 2007) and during 2005-2007, 111 birds were radio-tracked at Port Snettisham, Alaska, to determine nesting habitat, activity patterns and distribution (Nelson et al. 2008). A recommended protocol for surveying the species in forests was published in 2003 by PSG (Mack et al. 2003). In British Columbia standard protocols have been developed for various survey methods (RISC 2001, Manley 2006). Research has shown that habitat management at relatively fine scales may provide conservation benefits (Horton 2008) and that the species would benefit from a reduction in the amount of hard edges (recent clear-cuts) at both patch and landscape scales (Malt and Lank 2007, 2009).
|Amended reason:||Edited: Geographic Range, Population Justification, Rationale, Habitat and Ecology, Countries of Occurence, Threats, Conservation Actions proposed, Underway and in Place, Important Conservation Actions Needed and Research Needed. Added references and also added new Contributors and a new Compiler.|
|Citation:||BirdLife International. 2017. Brachyramphus marmoratus. (amended version published in 2016) The IUCN Red List of Threatened Species 2017: e.T22694870A112447662.Downloaded on 24 June 2017.|
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