Sephanoides fernandensis 

Scope: Global
Language: English

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Taxonomy [top]

Kingdom Phylum Class Order Family
Animalia Chordata Aves Caprimulgiformes Trochilidae

Scientific Name: Sephanoides fernandensis (King, 1831)
Common Name(s):
English Juan Fernandez Firecrown, Juan Fernández Firecrown
Spanish Colibrí de Juan Fernández
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: 13 cm. Entirely rufous hummingbird. Male bright rufous-orange, with dusky flight feathers. Reddish-yellow crown, generally appearing dark. Dusky lores. Immature male has rufous spotting on crown. Female dark green above, with bluish tinge on crown. Whitish underparts, densely spotted dark green on throat, extending on to flanks. Similar spp. Female Green-backed Firecrown S. sephanoides is smaller, paler green with duskier underparts and not so densely spotted on throat, with white postocular spot.

Assessment Information [top]

Red List Category & Criteria: Critically Endangered B1ab(i,ii,iii,v) ver 3.1
Year Published: 2016
Date Assessed: 2016-10-01
Assessor(s): BirdLife International
Reviewer(s): Butchart, S. & Symes, A.
Contributor(s): Hodum, P., Torres-Mura, J. & Hahn, I.
Facilitator/Compiler(s): Benstead, P., Bird, J., Butchart, S., Capper, D., Sharpe, C J, Symes, A. & Khwaja, N.
This species has an extremely small range, restricted to fragmented habitat on a single island, where habitat loss, predation by introduced mammals and possibly competition are causing continuing declines. It consequently qualifies as Critically Endangered.

Previously published Red List assessments:

Geographic Range [top]

Range Description:Sephanoides fernandensis is endemic to the Juan Fernández Islands, Chile, where the nominate race is confined to c. 11 km2 on Isla Robinson Crusoe. The race leyboldi is extinct on Isla Alejandro Selkirk, where it was last recorded in 1908. Historical records indicate that densities on Robinson Crusoe were formerly much greater than the 684 individuals (varying between 804 birds in the austral summer and 445 in autumn) estimated in 1988-1989. Direct count surveys in 1995-1997 indicated that the population is in the low hundreds (Roy et al. 1999), and transect counts were used in 2001-2002 to estimate a total population of 1,258 individuals (Hahn et al. 2006). However, more thorough surveys conducted in 2005 and repeated in 2006, coupled with quantitative modelling, estimated population densities in different habitats and concluded that the global population is considerably larger: c.2,500-3,000 individuals (P. Hodum in litt. 2007, 2008).

Countries occurrence:
Additional data:
Continuing decline in area of occupancy (AOO):Yes
Extreme fluctuations in area of occupancy (AOO):NoEstimated extent of occurrence (EOO) - km2:12
Continuing decline in extent of occurrence (EOO):YesExtreme fluctuations in extent of occurrence (EOO):No
Number of Locations:1Continuing decline in number of locations:Unknown
Extreme fluctuations in the number of locations:No
Upper elevation limit (metres):800
Range Map:Click here to open the map viewer and explore range.

Population [top]

Population:A survey in 2011 using line transect and banding counts estimated the population at 740 individuals, equating to 490 mature individuals, this figure is considerably lower than previous estimates as a result of the tsunami in 2010 (Hahn et al. 2015) and the population is likely to have recovered slightly by now (I. Hahn in litt. 2015). The population was previously estimated to number 2,500-3,000 individuals in total, roughly equating to 1,700-2,000 mature individuals (P. Hodum in litt. 2007). The current population is therefore estimated at a minimum of 490 mature individuals or 740 individuals.

Trend Justification:  The species is suspected to be decreasing at a rate of 1-9% over ten years, owing to the combined threats of habitat loss and degradation, predation and competition within its tiny range.

Current Population Trend:Decreasing
Additional data:
Number of mature individuals:490-2000Continuing decline of mature individuals:Yes
Extreme fluctuations:NoPopulation severely fragmented:No
No. of subpopulations:1Continuing decline in subpopulations:Unknown
Extreme fluctuations in subpopulations:NoAll individuals in one subpopulation:Yes
No. of individuals in largest subpopulation:100

Habitat and Ecology [top]

Habitat and Ecology:It inhabits remnant native forests, on which it appears to be completely dependent for breeding (there is a strong negative correlation between the presence of non-native vegetation and the location of nests [Hodum in litt. 2007, 2008]), but also utilises non-native plant communities during the non-breeding season, feeding on introduced plants, such as Eucalyptus globulus and garden flowers. This usage of non-native plants is especially common in the austral autumn and winter when only one native species (Raphithamnus venustus) flowers (Roy et al. 1999). It feeds on the endemic Cabbage Tree (Dendroseris litoralis) in late summer (Hahn et al. 2015). It is mostly nectarivorous, but small insects are taken from leaves or in flight. The proportion of insects in the diet increases during the chick-rearing period. The sex ratio is heavily skewed, with three males to every female (Roy et al. 1999). It may experience competition with S. sephaniodes, especially over access to Dendroseris litoralis flowers post-breeding (López-Calleja et al. 2006).

Continuing decline in area, extent and/or quality of habitat:Yes
Generation Length (years):4.2
Movement patterns:Not a Migrant

Threats [top]

Major Threat(s): The clearance and degradation of vegetation by humans since the late 16th century and the impacts of herbivorous mammals (especially rabbits introduced in the 1930s) has limited the availability, quantity and quality of food resources. Wood harvesting at lower altitudes has contributed to the loss of native habitat (Roy et al. 2013). Habitat quality is also being degraded by the spread and dominance of invasive plants, most prominently by Elm-leaf Blackberry Rubus ulmifolius, Maqui Aristotelia chilensis and Murtilla Ugni molinae (Anon. 2005). Introduced predators, such as rats, cats and coatis, have been implicated in the mortality of some birds and may be responsible in part for its decline (Roy et al. 1999, Hahn and Römer 2002). Cats have been documented killing firecrowns in town during the non-breeding season (Hodum in litt. 2007, 2008). Austral Thrush Turdus falcklandii has been observed predating firecrown nests and may represent a threat (Hahn et al. 2011a). As is true with many island species, firecrowns are easily approached, thus rendering them highly susceptible to predation. Additionally, during its nocturnal torpor, this species is presumed to be very vulnerable to predation (Hahn and Römer 2002).

Males are able to defend territories with highly productive resources, but the smaller females are possibly being indirectly outcompeted by S. sephaniodes (Roy et al. 1999, Wolf 2008). Observations of interactions between the two species in 2006-2007 found no evidence that male fernandensis were negatively affected by S. sephaniodes, but that female fernandensis may suffer from interference competition and may be marginalised from high quality foraging habitat (Wolf and Hagen 2012). S. sephaniodes prefers sites with denser vegetation, higher species diversity and located less high off the ground, and therefore may not constrain nesting habitat use by S. fernandensis; alternatively competitive displacement for nest site choices may already have occurred (Hahn et al. 2011a).

Preliminary analyses of the population revealed some genetic variation, but significantly less than in S. sephaniodes (Roy et al. 1999). A devastating tsunami in February 2010, which destroyed the only town on Robinson Crusoe had a significant impact on the species, reducing the population to 740 individuals in March 2011 (I. Hahn in litt. 2015). Seasonally important populations of the endemic Cabbage Tree (Dendroseris litoralis) in the coastal zone were lost as a result of the tsunami which resulted in a reduction in the local abundance of Juan Fernandez Firecrown (Hahn et al. 2015). The disaster likely also reduced cat predation.

Conservation Actions [top]

Conservation Actions: Conservation Actions Underway
CITES Appendix II. The Juan Fernández Islands were designated as a national park in 1935 (protected from 1967) and an UNESCO Biosphere Reserve in 1977. The Chilean government began restoring habitat in 1997 (J. C. Torres-Mura in litt. 1999), and the islands have been nominated for World Heritage listing (Hulm 1995). Conservation is being led by the Juan Fernández Islands Conservancy, with support from the American Bird Conservancy, Conservation International, the Hummingbird Society, the Juan Fernandez Islands Conservancy (a program of Oikonos Ecosystem Knowledge), and the Royal Society for the Protection of Birds. Key activities which have already taken place are (Hodum and Tomé 2005, Hodum in litt. 2007, 2008): the hiring of two island residents as project coordinators; control of invasive plants and herbivores (including volunteer programmes for island residents to participate in invasive plant removal), which appears to increase nesting success of the species; invasive predator control (including cat control in the town on Robinson Crusoe); habitat restoration in native forest; a community outreach programme aimed at engaging local people (Anon 2005) and including environmental education programmes for local schoolchildren; as well as population surveys and monitoring of active nests, phenology and reproductive success. The endemic plant Dendroseris litoralis has been planted in settlement areas to provide nectar resources for the species (Hahn et al. 2011b). The population has been monitored since 2006, and a workshop on terrestrial bird census techniques was organized for local people in October 2011, aimed at forming a local team that can carry out regular bird censuses; a pilot project was implemented to test the capacity of the trained team of local fieldworkers to gather data by using a monitoring protocol.

Conservation Actions Proposed
Continue to monitor the population using a quantitative census methodology that allows for statistical comparisons between surveys. Remove all introduced mammals, initially within an intensively managed, fenced, feasibility study area (Roy et al. 1999). Replant native flora (including a 10 ha plot with shrubs that flower throughout the year) in areas free of introduced rabbits and cattle, initially within the feasibility study area but also at forest edges (Roy et al. 1999). Ensure that Cabbage Trees that were destroyed by the 2010 tsunami are replanted (Hahn et al. 2015). Enforce grazing restrictions on national park land (Roy et al. 1999). Evaluate feasibility of establishing feeding stations in native forest. Replant fast-growing, soil-binding trees along highly eroded slopes for short-term relief (Roy et al. 1999). Implement systematic introduced plant control zonally (Roy et al. 1999). Continue to support ongoing efforts to remove alien invasive plants and mammalian predators, and increase awareness. Support efforts by CONAF to cultivate endemic plants that serve as food resources for the species (P. Hodum in litt. 2012). Urgently investigate scale of predation risk from Austral Thrush and consider control measures if appropriate (Hahn et al. 2011a). Undertake research to evaluate genetic variation and inbreeding depression within the population (Roy et al. 2013).

Citation: BirdLife International. 2016. Sephanoides fernandensis. The IUCN Red List of Threatened Species 2016: e.T22687863A93172411. . Downloaded on 24 September 2017.
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