Data Zone
Justification of Red List category
Black-winged Lory has a small range and is undergoing a continuing decline in the number of mature individuals but the population size is suspected to exceed the thresholds for listing as threatened. The species has been heavily targeted for the illegal bird trade on Biak, but remains commoner elsewhere in the small range. Rapid rates of reduction in abundance on Biak reported between 1982 and 1997 appeared to have slowed in the 2000s (after importation to the EU was banned and controls on exports tightened) and encounter rates appear similar for visits over the past decade. However, high rates of trapping have been noted on Biak again recently, leading to the inference that there is an ongoing reduction in the number of mature individuals, potentially compounded by current (albeit relatively low) rates of forest cover loss. While trapping poses a threat that may apply across the population, the number of locations only approaches the threshold for listing as threatened. As such, it is assessed as Near Threatened.
Population justification
The species is generally common on the island of Biak (Beehler and Pratt 2016), despite reports of abundance having declined between 1982 and 1995 (K. D. Bishop in litt. 2000). There are no published estimates of population or density for Black-winged Lory. The plausible range of population can be inferred from the densities of congeners and the area of forest habitat within the range of the species. Other species in the genus Eos have been studied on a number of islands with an average abundance of 47 individuals per km2 (from 28 reported density estimates: Santini et al. 2018). The area of forest within the range (Biak and surrounding small islands, Numfor Manim and Num) totals 1,756 km2 (extracted from the GlobCover 2 land cover layer [Arino et al. 2012]). If half of the area were to be occupied at the average density reported for Eos lories, the population would be 41,317 individuals, with the 25-75 percentile range of densities giving a range of 11,743-67,386 individuals. This indicative population size suggests that the species is likely to exceed the threshold for listing as threatened under the small and declining population size criterion.
While individuals and groups move extensively in the search for fruiting and flowering trees, these movements are similar to those undertaken by other members of the genus, and are of small scale hence are not considered to represent genuine nomadic movements. As such, while the species is obviously capable of crossing stretches of sea to reach other islands, it is plausible that there are up to four subpopulations, and two is the most likely number (Numfor and Biak/Supiori with the minor islands).
Trend justification
Previously, rapid reductions in the abundance of the species were noted due to high levels of trapping on Biak (K.D. Bishop in litt. 2000). In the past few years there are once again reports of high trapping rates impacting the Biak population (Bergmark 2019, M. Halaouate in litt. 2022). As such, the number of mature individuals is again inferred to be declining. Trapping does not appear to be a significant problem elsewhere in the range and the species remains much commoner on Numfor than it is now on Biak (M. Halaouate in litt. 2022). The maximum rate of forest cover loss have been 6.3% over the past three generations (data from Global Forest Watch 2021, using Hansen et al. [2013] data and methods disclosed therein). The species is tolerant of forest degradation and utilises tree crops and secondary forest, hence it is unclear whether this rate of forest cover loss would cause an equivalent rate of population reduction, however it is judged likely that this level of forest cover loss would lead to a reduction in the available habitat for the species, as well as a decline in habitat quality and potentially correlates with greater trapping access to previously safe parts of Biak.
Accordingly, the species is inferred to be suffering a continuing decline in the number of mature individuals. Based on a) the species having some tolerance for forest loss, hence assuming a population impact that is half the rate of the estimated forest loss rate, and b) the impact of trapping adding at least 5% to the rate of population reduction over three generations, a suspected rate of reduction is tentatively placed within the range of 1-9% over the past three generations, and currently this is the rate that is suspected to continue into the future. However, there is a need for an urgent investigation to quantify the current impact of trapping on all targeted species on these islands, and reports of reduced abundance on islands aside from Biak will lead to the suspicion that rates of reduction may be higher.
Eos cyanogenia is endemic to the Geelvink Islands of Papua (formerly Irian Jaya), Indonesia, where it is known from the islands of Biak-Supiori, and the much smaller islands of Numfor, Manim and Mios Num (Mayr and Meyer de Schauensee 1939, Beehler et al. 1986, Beehler and Pratt 2016, Collar and Boesman 2020). There are additional records on the very small Owi and Wundi islands (eBird 2021), suggesting that it may be present on many of the satellite islands southeast of Biak. On Biak, it is fairly common to common in patchy forest, and is sometimes recorded in flocks of 40-60 (Gibbs 1993, Collar et al. 1994, eBird 2021). On Supiori, it is common, although less so at higher altitudes (Bishop 1982, Gibbs 1993): it appears commoner in plantations and degraded forest rather than primary forest inland (Mayr and Meyer de Schauensee 1939). It is nomadic, making it difficult to assess its true numbers but, on Biak, it has been reported that it declined notably between 1982 and 1995 (K. D. Bishop in litt. 2000).
It is a gregarious species which apparently feeds chiefly in inland forest, up to 460 m (although becoming less common at altitudes above 200 m on Supiori, at least), and roosts in coconut plantations and nearby coastal forest (Bishop 1982). Mayr and Meyer de Schauensee (1939) describe it as being less abundant in intact inland forest and more frequent in secondary habitats. It is common in "flat forest" on Supiori (Gibbs 1993) but is absent from low scrubby regrowth (K. D. Bishop in litt. 2000).
Relatively large numbers were previously trapped for the domestic and international trade (Nash 1990, K. D. Bishop in litt. 1994), and this species was commonly observed as a pet on Biak (Bishop 1982). Recently trapping pressure has been reported to be high and causing further declines on Biak (Bergmark 2019, M. Halaouate in litt. 2022), noting that numbers were previously reduced here (K. D. Bishop in litt. 2000).
Forest on Biak has come under heavy pressure from logging and subsistence farming, though large-scale logging has not been economically feasible for some time (Wikramanayake et al. 2002). The rate of forest cover loss recorded through satellite monitoring has been slow in the past two decades, and over the past three generations of the species the maximum rate is estimated at 3.6% (data from Global Forest Watch 2021, using Hansen et al. [2013] data and methods disclosed therein). The species is tolerant of degraded forest but does require forest cover, hence it is unclear that this low rate of forest cover loss will be driving a significant population reduction. Much of Supiori comprises virtually impenetrable, forested limestone mountains, which is likely to be safe from habitat degradation.
Large areas of forest on Biak have previously been destroyed or damaged by logging and subsistence farming, particularly the southern plains (Bishop 1982, K.D. Bishop in litt. 1996, D. Holmes in litt. 2000). Forest regeneration is slow on areas of raised coralline limestone, which comprises most of Biak. There is also a proposal for a spaceport on the eastern side of Biak, which would cause the loss of 6.5km2 of Protection Forest (Perwitasari and Susanti 2019) and may result in further development (e.g. expanded and improved road infrastructure and increased settlement in the area).
Conservation Actions Underway
CITES Appendix II. There are two protected areas on the islands, Biak-Utara (covering 110 km2) and Pulau Supiori (covering 420 km2) Nature Reserves (Sujatnika et al. 1995). It was common in Biak-Utara Reserve in 1997 (B. Beehler and S. van Balen in litt. 2000).
10 cm. Bright red, long-tailed parrot. Violet patch on ear-coverts and black mantle and wing-coverts. Red underwing, yellowish subterminally with narrow black trailing edge. Similar spp. Black-capped Lory Lorius lory has short tail, black cap, green upperwings and purple belly. Red-fronted Lorikeet Charmosyna rubronotata and Coconut Lorikeet Trichoglossus haematodus are largely green. Voice Stronger and shorter screech than T. haematodus. Hints Fairly common around any remnant forest, especially at flowering trees.
Text account compilers
Martin, R.
Contributors
Beehler, B.M., Benstead, P., Bird, J., Bishop, K.D., Bostock, N., Crosby, M., Derhé, M., Dutson, G., Halaouate, M., Holmes, D., van Balen, B.S. & van Beirs, M.
Recommended citation
BirdLife International (2024) Species factsheet: Black-winged Lory Eos cyanogenia. Downloaded from
https://datazone.birdlife.org/species/factsheet/black-winged-lory-eos-cyanogenia on 28/12/2024.
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 28/12/2024.