Inferring extinction in North American and Hawaiian birds in the presence of sighting uncertainty
- Academic Editor
- Stuart Pimm
- Subject Areas
- Biodiversity, Conservation Biology, Zoology
- Avian extinction, Conservation triage, Critically endangered, Sighting records, Sighting reliability, Species persistence
- © 2016 Roberts and Jarić
- This is an open access article distributed under the terms of the Creative Commons Attribution License, which permits unrestricted use, distribution, reproduction and adaptation in any medium and for any purpose provided that it is properly attributed. For attribution, the original author(s), title, publication source (PeerJ) and either DOI or URL of the article must be cited.
- Cite this article
- 2016. Inferring extinction in North American and Hawaiian birds in the presence of sighting uncertainty. PeerJ 4:e2426 https://doi.org/10.7717/peerj.2426
For most species the timing of extinction events is uncertain, occurring sometime after the last sighting. However, the sightings themselves may also be uncertain. Recently a number of methods have been developed that incorporate sighting uncertainty in the inference of extinction based on a series of sightings. Here we estimate the timing of extinction for 41 of 52 North American and Hawaiian bird taxa and populations, the results of which suggest all became extinct before 2009. By acknowledging sighting uncertainty it results in two opposite effects, one pushing the timing of extinction away from the last sighting and the other drawing the timing of extinction nearer to it. However, for 14 assessed taxa and populations the upper 95% bounds lie beyond the end of the observation period and therefore suggest the possibility of continued persistence. This has important implications for conservation decision-makers and potentially reduces the likelihood of Romeo’s Error.
For many species our knowledge of their persistence is based on sightings that vary in quality and therefore the level of reliability (Roberts, Elphick & Reed, 2010). For species that are approaching extinction or that may already be extinct acknowledging this uncertainty can have profound effects on conservation decision-making, as erroneous evidence based on uncertain sightings can result in wasted resources (McKelvey et al., 2008). For example in 2005, based on a brief sighting and a pixelated image, the ivory-billed woodpecker was declared to have been rediscovered (Fitzpatrick et al., 2005), resulting in the mobilisation of resources for management strategies and recovery plans (Gotelli et al., 2012). However, based on the evidence its rediscovery was brought into question (Sibley et al., 2006), and subsequent extensive searches have failed to result in further sightings (Gotelli et al., 2012)
Several methods have been developed for the inference of extinction based on sighting data (see Solow, 2005 for a review), however until recently, these methods treated all sightings as certain. It has therefore been the responsibility of those using the methods to decide what data should be used and what should be discarded. Recently a number of methods have been developed that incorporate uncertainty (e.g., Solow et al., 2012; Jarić & Roberts, 2014; Lee et al., 2014).
Elphick, Roberts & Reed (2010) estimated the time of extinction for 38 of 52 North American and Hawaiian bird taxa and populations that are thought to be potentially extinct, along with the likelihood of extinction by 2009. In the study they based their analysis on sightings that are assumed to have the highest level of reliability (e.g., museum specimens), and then repeated the analysis by including additional sightings for which sufficient documentation exists to satisfy experts. In this way Elphick, Roberts & Reed (2010) attempted to acknowledge the issue of sighting uncertainty and incorporate it into their analysis on an ad hoc based criteria. Their analysis, however, excluded a number of controversial sightings that experts disagreed as to whether they should be accepted. In this paper we revisit this study, using a method that explicitly incorporates sighting uncertainty (Jarić & Roberts, 2014), to investigate the impact of accounting for sighting uncertainty when inferring extinction.
We apply here the approach of Jarić & Roberts (2014) that represents a modification of the existing methods for inferring extinction based on sighting records, which allows for inclusion of specific sighting reliabilities of individual observations. In line with the original approach, we apply it to the standard Solow method (Solow, 1993), which was also used to infer extinction by Elphick, Roberts & Reed (2010). For details on Solow method modification, see Jarić & Roberts (2014) as well as Supplemental Information 1.
We revisited the 52 North American bird taxa and populations assessed by Elphick, Roberts & Reed (2010) that are presumed to be extinct, or whose persistence is a point of discussion. In their study and used here, Elphick, Roberts & Reed (2010—supplementary material) compiled sighting records for all taxa but divided the sightings into three categories that form a nest hierarchy:
Physical Evidence (PE)—e.g., museum specimens, but also uncontroversial photographs, video, and sound recordings.
Independent Expert Opinion (IEO)—evidence that experts deemed sufficiently documented to confirm the record.
Controversial sightings (CS)—sightings judged to lack firm evidence including any sighting for which there is published disagreement between experts.
Elphick, Roberts & Reed (2010) used the method of Solow (1993) for the inference of extinction (but also see Solow, 2005) and based their analysis on PE and PE + IEO, but excluded CS. Following Jarić & Roberts (2014), who applied the sighting reliability scoring system used by BirdLife International (Table 1 of Lee et al., 2014), we assign PE sightings (i.e., Lee et al.’s “Record described as being based on collected individual”) with a lower limit of reliability of 0.8, and upper limit of 0.9 and a mean of 0.85. This was repeated for IEO (i.e., Lee et al.’s “Record based on observation described in the literature as ‘confirmed’ or considered fairly convincing”) and CS (i.e., Lee et al.’s “Record described in the literature as (or judged to be) unconfirmed or questionable”), 0.6, 0.8, 0.7 and 0.1, 0.4, 0.25 respectively.
First sightings in each sighting record dataset were used to establish the beginning of the sighting period, and excluded from the analysis (Solow, 2005). Minimum number of sightings in a sighting record (n ≥ 5, i.e., 4 following the exclusion of the first sighting) was defined in line with Solow (2005) and Elphick, Roberts & Reed (2010). Consequently, analyses were conducted only for sighting records and reliability score setups with the most likely number of observations (r value, see Jarić & Roberts, 2014) of at least 3.5 (i.e., excluding the reliability score for the first sighting). The approach was used to estimate the p value for each species (with T = 2009 in line with Elphick, Roberts & Reed, 2010), probable extinction time (TE) and the upper bound (TCI) of a 1-α confidence interval (α = 0.05).
Of the 52 taxa and populations, there were sufficient sightings to conduct analyses for 41, compared with 38 taxa and populations analyzed by Elphick, Roberts & Reed (2010). Estimated extinction dates (TE) ranged from 1855 to 2008, with the upper 95% bounds (TCI) on these estimates ranging from 1863 to 2113 (Table 1). Based on these analyses, there is no indication that any taxa and populations are likely to persist, including the ‘Alalā (Hawaiian crow, Corvus hawaiiensis) which was the only taxa in Elphick, Roberts & Reed’s (2010) study for which there was any indication of likely persistence. Taxa and populations for which the 95% confidence interval around the predicted extinction date includes dates after 2008 were Eskimo Curlew (Numenius borealis), Ivory-billed woodpecker (Campephilus principalis), ‘Alalā (Hawaiian crow), Kaua‘i ‘ō‘ō (Moho braccatus), O‘ahu ‘ō‘ō (M. apicalis), Kama‘o (Myadestes myadestinus), Oloma‘o (Moloka‘i) (M. lanaiensis rutha), ‘Ō‘ū (Kaua‘i) (Psittirostra psittacea), Nukupu‘u (Kaua‘i) (Hemignathus lucidus hanapepe), Nukupu‘u (Maui) (H. l. affinis), O‘ahu ‘alauahio (Paroreomyza maculata), Maui ‘akepa (Loxops coccineus ochraceus), Oahu ‘akepa (L. c. rufus) and the Po‘o-uli (Melamprosops phaeosoma) (indicated in bold in Table 1). In comparison, Elphick, Roberts & Reed’s (2010) analysis only observed such confidence intervals for the ‘Alalā (Hawaiian crow), as well as partly for Kama‘o, O‘ahu ‘alauahio and the Po‘o-uli (i.e., they had TCI > 2009 only when using PE, while for PE + IEO combination it was TCI < 2009). Elphick, Roberts & Reed (2010) only provided sighting data to 2009, and therefore other, most likely controversial, sightings may have occurred during the following years, assuming no further sightings have actually occurred since 2009. Taxa and populations for which the 95% confidence intervals around the predicted extinction dates include dates after 2016 were ‘Alalā (Hawaiian crow), Oloma‘o (Moloka‘i), Nukupu‘u (Kaua‘i), Nukupu‘u (Maui), O‘ahu ‘alauahio, Maui ‘akepa and the Oahu ‘akepa (Table 1).
|Species||IUCN Red List||Last sighting||n||Sighting reliability||p||TE||TCI|
|Labrador duck (Camptorhynchus labradorius)||EX||1878||13||Upper||3E−7||1880||1889|
|Heath hen (Tympanuchus c. cupido)||EX||1932||39||Upper||4E−15||1933||1936|
|Laysan rail (Zapornia palmeri)||EX||1945||29||Upper||7E−9||1946||1951|
|Hawaiian rail (Zapornia sandwichensis)||EX||1893||9||Upper||0.010||1905||1956|
|Eskimo curlew (Numenius borealis)||CR(PE)||2006||49||Upper||0.062||2003||2010|
|Great auk (Pinguinus impennis)||EX||1888||24||Upper||8E−10||1872||1879|
|Passenger pigeon (Ectopistes migratorius)||EX||1907||26||Upper||3E−15||1906||1909|
|Carolina parakeet (Conuropsis carolinensis)||EX||1950||50||Upper||1E−10||1946||1950|
|Ivory-billed woodpecker (Campephilus principalis)||CR||2006||68||Upper||0.065||2005||2010|
|‘Alalā (Hawaiian crow) (Corvus hawaiiensis)||EW||2003||68||Upper||0.220||2007||2015|
|Kaua’i ‘ō‘ō (Moho braccatus)||EX||2001||43||Upper||0.103||2002||2013|
|O‘ahu ‘ō‘ō (Moho apicalis)||EX||1976||10||Upper||0.292||1994||2113|
|Bishop’s ‘ō‘ō(Moloka‘i) (Moho bishopi)||EX||1904||5||Upper||3E−4||1907||1919|
|Hawai‘i ‘ō‘ō (Moho nobilis)||EX||1976||24||Upper||0.008||1974||1991|
|San Clemente [Bewick’s] wren (Thryomanes bewickii leucophrys)||–||1941||20||Upper||7E−7||1944||1951|
|Laysan millerbird (Acrocephalus f. familiaris)||EX||1916||12||Upper||2E−6||1919||1927|
|Kama‘o (Myadestes myadestinus)||EX||1999||50||Upper||0.069||2001||2011|
|Oloma‘o (Moloka‘i) (Myadestes lanaiensis rutha)||CR(PE)||2005||16||Upper||0.188||2001||2025|
|Oloma‘o (Lāna‘i) (Myadestes l. lanaiensis)||CR(PE)||1934||9||Upper||0.001||1941||1960|
|Bachman’s warbler (Vermivora bachmanii)||CR(PE)||2001||61||Upper||0.004||1997||2002|
|Dusky seaside sparrow (Ammodramus maritimus nigrescens)||EX||1980||48||Upper||6E−5||1983||1988|
|‘Ō‘ū (Kaua‘i) (Psittirostra psittacea)||CR(PE)||1997||33||Upper||0.057||2000||2010|
|‘Ō‘ū (Hawai‘i) (Psittirostra psittacea)||CR(PE)||1987||42||Upper||0.004||1990||1998|
|‘Ō‘ū (Moloka‘i) (Psittirostra psittacea)||CR(PE)||1965||6||Upper||0.015||1940||1978|
|‘Ō‘ū (Lāna‘i) (Psittirostra psittacea)||CR(PE)||1927||8||Upper||9E−4||1933||1951|
|‘Ō‘ū (Maui) (Psittirostra psittacea)||CR(PE)||1945||7||Upper||0.004||1927||1954|
|Greater koa-finch (Rhodacanthis palmeri)||EX||1967||8||Upper||0.007||1943||1970|
|Greater ‘amakihi (Hemignathus sagittirostris)||EX||1901||5||Upper||9E−5||1903||1912|
|Lesser ‘akialoa (Hemignathus obscurus)||EX||1940||19||Upper||5E−6||1923||1934|
|Greater ‘akialoa (Kaua‘i) (Hemignathus ellisianus stejnegeri)||EX||1995||21||Upper||0.027||1991||2004|
|Nukupu‘u (Kaua‘i) (Hemignathus lucidus hanapepe)||CR(PE)||1996||24||Upper||0.179||2002||2022|
|Nukupu‘u (Maui) (Hemignathus lucidus affinis)||CR(PE)||1996||24||Upper||0.256||2004||2029|
|O‘ahu ‘alauahio (Paroreomyza maculata)||CR(PE)||2002||46||Upper||0.218||2006||2019|
|Maui ‘alauahio (Lāna‘i) (Paroreomyza montana)||EX||1937||10||Upper||7E−4||1942||1958|
|Kākāwahie (Paroreomyza flammea)||EX||1963||16||Upper||0.006||1970||1987|
|Maui ‘akepa (Loxops coccineus ochraceus)||EX||1995||21||Upper||0.147||2001||2019|
|Oahu ‘akepa (Loxops coccineus rufus)||EX||1976||7||Upper||0.125||1965||2053|
|Hawai‘i mamo (Drepanis pacifica)||EX||1960||12||Upper||0.033||1943||1996|
|Black mamo (Drepanis funerea)||EX||1955||6||Upper||0.024||1944||1987|
|Laysan honeycreeper [‘apapane] (Himatione sanguinea freethii)||EX||1923||14||Upper||6E−4||1930||1950|
|Po‘o-uli (Melamprosops phaeosoma)||CR(PE)||2004||27||Upper||0.037||2005||2009|
Incorporating uncertainty in the inference of extinction of a species has two effects that run counter to each other, one potentially pushing forward the date of extinction and the other drawing it to an earlier year. Firstly, by reducing the reliability from 1.0 it increases uncertainty in the date of extinction and therefore results in the inferred persistence of the taxa being potentially pushed beyond those inferred through methods that do not incorporate uncertainty. Secondly, however, by allowing for the incorporation of uncertainty it is possible to incorporate controversial sightings (i.e., Elphick, Roberts & Reed, 2010 only incorporate PE and IEO). This results in more sightings within a record and therefore fewer gaps between years in the sighting record, thus potentially drawing the extinction date closer to the time of the last sighting, although the date of the last sighting is by definition uncertain (see Jarić & Roberts, 2014).
In this study, by incorporating sighting uncertainty into the inference of extinction it allowed us to assess an additional 3 taxa and populations beyond Elphick, Roberts & Reed’s (2010) 38, due to the additional data this brings from the controversial sightings. Furthermore, the number of taxa and populations for which the 95% confidence interval around the predicted extinction date includes dates after 2008 increased from 6 to 14. This has potentially important implications in terms of conservation management and the distribution of resources for the additional 8 taxa and populations. Further, improper classification of these taxa could have resulted in Romeo’s Error (Collar, 1998), where the taxon is assumed to be extinct, which results in a lack of appropriate and timely conservation efforts, and consequently precipitates its true extinction.
Sighting observations of species or individuals are likely to have some level of uncertainty as to whether a correct identification has been made. Few have, however, attempted to quantify the level of uncertainty (e.g., Lee et al., 2015), test for the level of accuracy experimentally (e.g., Gibbon, Bindemann & Roberts, 2015) or incorporated this into their analyses (e.g., Jarić & Roberts, 2014; Lee et al., 2014). As we have shown here, acknowledging such uncertainties can have a profound impact on decision-making; in the case of a critically endangered species, it may influence whether it is considered extinct or extant and therefore whether conservation efforts and resources should be allocated. For some species, extinction may occur within years of being described as a new taxon to science. As an example, a cryptically coloured treehunter from Brazil, Cichlocolaptes mazarbarnetii, described in 2014, was last seen in 2007, but had lain misidentified in the National Museum of Brazil for over 20 years having been collected in 1986 (Lees & Pimm, 2015).
Finally, while we incorporated sighting uncertainty into a time-based extinction model, such sightings with spatial data are frequently used in occupancy modelling with apparently little consideration to the underlying uncertainty of the identification (but see Romero et al., 2014). This is likely to be particularly an issue when using historic sightings, whose location data may also be imprecise. Much of this data is becoming increasingly available online and can be accessed rapidly. However, consideration should be given to the quality of the data, including spatial and temporal inaccuracies (Yesson et al., 2007), particularly identification uncertainties.