COSEWIC assessment and update status report on the Ermine (haidarum subspecies) in Canada 2001

COSEWIC
assessment and update status report
on the
Ermine haidarum subspecies
Mustela erminea haidarum
in Canada

Ermine haidarum subspecies (Mustela erminea haidarum)

Threatened
2001



COSEWIC
Committee on the status
of endangered wildlife
in Canada
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COSEPAC

Comité sur la situation
des espèces en péril
au Canada


COSEWIC status reports are working documents used in assigning the status of wildlife species suspected of being at risk. This report may be cited as follows:

Please note: Persons wishing to cite data in the report should refer to the report (and cite the author(s)); persons wishing to cite the COSEWIC status will refer to the assessment (and cite COSEWIC). A production note will be provided if additional information on the status report history is required.

COSEWIC 2001. COSEWIC assessment and update status report on the Ermine haidarim subspecies Mustela erminea haidarum in Canada. Committee on the Status of Endangered Wildlife in Canada. Ottawa. vi + 41 pp.
(Species at Risk Status Reports)

Edie, A. 2001. Update COSEWIC status report on the Ermine haidarum subspecies Mustela erminea haidarumi in Canada, in COSEWIC assessment and update status report on the Ermine haidarim subspecies Mustela erminea haidarum in Canada. Committee on the Status of Endangered Wildlife in Canada. Ottawa. 1-41 pp.

Youngman, P. 1984. COSEWIC status report on the Ermine Mustela erminea haidarumi (Queen Charlotte Islands population) in Canada. Committee on the Status of Endangered Wildlife in Canada. Ottawa. 14 pp.

Ermine haidarum subspecies Mustela erminea haidarum was previously designated by COSEWIC as Ermine Mustela erminea haidarum (Queen Charlotte Islands population).

Également disponible en français sous le titre Évaluation et Rapport de situation du COSEPAC sur la situation de l'hermine de la sous-espèce haidarum (Mustela erminea haidarum) au Canada - Mise à jour.

Cover illustration:
Ermine Haidarum Subspecies -- illustration by Judie Shore.

© Her Majesty the Queen in Right of Canada 2004
Catalogue No.: CW69-14/231-2002E-IN
ISBN: 0-662-32919-8

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Assessment summary – May 2001

Common name:
Ermine haidarum subspecies

Scientific name:
Mustela erminea haidarum

Status:
Threatened

Reason for designation:
A distinct subspecies that appears to have greatly declined in density and whose habitat has been severely affected by introduced mammals. A comparison of results of a recent, intensive sampling program with historic trapping records suggests a decline in numbers.

Occurrence:
British Columbia

Status history:
Designated Special Concern in April 1984. Status re-examined and designated Threatened in May 2001. Last assessment based on an update status report.

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The Queen Charlotte Islands (QCI) ermine (Mustela erminea haidarum) is a subspecies of the short-tailed weaselFootnote 1, Mustela erminea. Anatomical differences from other subspecies have led some investigators to suggest separate species status. Perhaps consistent with this suggestion, recent mtDNA evidence demonstrates that M. e. haidarum is part of one of three or perhaps four ancient evolutionary lineages in M. erminea, one found in Eurasia and Alaska, the other in most of the remainder of North America, and the third in Haida Gwaii and in a confined group of islands in nearby Southeast Alaska. A fourth lineage may exist on Vancouver Island, but genetic evidence is as yet preliminary. Differences in mtDNA among these lineages suggest separation considerably more ancient than the last glaciation, but precise dating is not possible with current understanding of mutation rates.

Once recent genetic data is fully considered, the Southeast Alaska population of the QCI lineage may, or may not, prove to be M. e. haidarum. In any case, the Alaska population has already been infiltrated by at least male if not female weasels of another lineage from the nearby mainland of Alaska. Consequently, the population of ermine in Haida Gwaii is the only example of the QCI lineage that is still genetically intact and likely to remain so. It is also the only known population of this lineage in Canada.

Understanding of other subspecies of M. erminea suggests that the QCI ermine is, as are all its conspecifics, a specialized predator adapted best to prey on arvicoline rodents (voles and lemmings). No arvicolines exist in Haida Gwaii, and Keen’s mouse (Peromyscus keeni) and dusky shrews (Sorex monticolus), the only native small mammals found in Haida Gwaii, appear to be poor substitutes. The relatively poor food supply available to the QCI ermine has probably always limited this animal to low densities, and continues to be a limitation today.

Since the Youngman (1984) status report on QCI ermine, considerable effort has been undertaken to document the status of the animal. Field work, including over 6700 trap-nights, some 2700 tracking station nights, and over 900km of snow tracking between 1992 and 1998, resulted in only 2 ermine captured, and identified no tracks or other sign. Another recent program comprised interviews of local persons in Haida Gwaii. Interviews were successful in documenting many previously unrecorded sightings of ermine or ermine sign. Analysis of available records suggests that the QCI ermine is not dependent on old growth forest, that it uses a wide variety of mostly low elevation habitats, and that it may preferentially use habitats near the ocean, rivers, creeks or estuaries. There is no indication that habitat, as separate from food supply or predation risk, is a serious limitation for the QCI ermine.

The QCI ermine appears to be very rare today, perhaps significantly rarer than it once was. While no definitive data exist, success of early mammal collectors in capturing ermine in the early 1900’s suggests that populations of ermine were probably considerably larger then than they are now.

Potential threats to the QCI ermine include the naturally poor food supply, predation by American marten (Martes americana), and exploitative and interference competition with marten and introduced red squirrel (Tamiasciurus hudsonicus), black rat (Rattus rattus), Norway rat (Rattus norvegicus) and raccoon (Procyon lotor). The existence and importance of predation and competition remain speculative. However, existing information suggests that predation by marten may be the most serious threat. Marten have been documented as predators of ermine elsewhere; marten in Haida Gwaii are known to readily scavenge ermine carcasses caught in traps; and marten hunting behaviour suggests strongly that they will kill and eat ermine whenever encountered.

The risk of predation by marten is not new. The threat arises from the fact that marten populations have increased dramatically, apparently in response to new food available from introduced mammals, primarily black-tailed deer (Odocoileus hemionus), red squirrel, black rat, Norway rat, and muskrat (Ondatra zibethica). Interviewed trappers are unanimous in their belief that marten populations have increased by a factor of between five and ten since the 1940’s, and marten populations in the 1940’s may have already been larger than historical ones as a result of introduction of black-tailed deer prior to 1916. Given the opportunistic hunting behaviour exhibited by marten, it seems likely that predation pressure on ermine populations has increased roughly in proportion to increases in marten populations, possibly by as much as an order of magnitude in comparison to historical levels. Introduced black-tailed deer may have exacerbated predation risk by widespread removal of shrubs that may have previously served as cover for ermine.

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The Committee on the Status of Endangered Wildlife in Canada (COSEWIC) determines the national status of wild species, subspecies, varieties, and nationally significant populations that are considered to be at risk in Canada. Designations are made on all native species for the following taxonomic groups: mammals, birds, reptiles, amphibians, fish, lepidopterans, molluscs, vascular plants, lichens, and mosses.

COSEWIC comprises representatives from each provincial and territorial government wildlife agency, four federal agencies (Canadian Wildlife Service, Parks Canada Agency, Department of Fisheries and Oceans, and the Federal Biosystematic Partnership), three nonjurisdictional members and the co-chairs of the species specialist groups. The committee meets to consider status reports on candidate species.

The Committee on the Status of Endangered Wildlife in Canada (COSEWIC) was created in 1977 as a result of a recommendation at the Federal-Provincial Wildlife Conference held in 1976. It arose from the need for a single, official, scientifically sound, national listing of wildlife species at risk. In 1978, COSEWIC designated its first species and produced its first list of Canadian species at risk. Species designated at meetings of the full committee are added to the list.

The Canadian Wildlife Service, Environment Canada, provides full administrative and financial support to the COSEWIC Secretariat.

Direct field data on the natural history and ecology of Queen Charlotte Islands ermine (Mustela erminea haidarum) are virtually non-existent. Consequently, accurate determination of life history characteristics and limiting factors is, at the time of this assessment, impossible. Further, given the near failure of intensive trapping recently undertaken to assess this subspecies, it is exceedingly unlikely that useful new data will become available soon. It appears that any management decisions potentially helpful for this subspecies, including classification under the Committee on the Status of Endangered Wildlife in Canada (COSEWIC) criteria, will have to be made with the very limited data currently available.

The task left to this review in these circumstances is to make the best possible use of the limited information available. Given the potential importance of insight into the biology of this sub-species, this report includes more speculation than some readers might think appropriate. This has been done deliberately in an attempt to ensure that as much information as possible may be applied to whatever decisions are made regarding this animal in the near future. Readers who consider the speculation unreasonable can, with the author’s apology, ignore it.

The Queen Charlotte Islands (QCI) have in recent years increasingly been referred to as Haida Gwaii in recognition of the fact that this archipelago is the ancestral homeland of the Haida first nation. In this report, Haida Gwaii refers to the Queen Charlotte Islands archipelago as a whole, and QCI ermine refers to Mustela erminea haidarum.

Queen Charlotte Islands (QCI) ermine (Mustela erminea haidarum L.) was first described as a new species Putorius haidarum (Preble, 1898), but is now recognized as a subspecies of the short-tailed weasel (Hall, 1951). In addition to the true weasels, the genus Mustela includes mink (M. vison) and ferrets (in North America, the black footed ferret, M. nigripes; Fagerstone, 1987).

Recent analysis of mitochondrial DNA (mtDNA) from some 200 ermine from western North America as well as Russia, Ireland and Japan indicates that Mustela erminea includes three highly divergent evolutionary lineages: the first from Europe, Asia, and most of Alaska; the second from most of S.E. Alaska, Western Canada and the rest of the continental U.S.A.; and the third from Haida Gwaii and the Prince of Wales group of islands in S.E. Alaska, directly across Dixon Entrance from the northern end of Haida Gwaii (Fleming and Cook, 2000). Preliminary evidence suggests that ermine on Vancouver Island may comprise a fourth similarly ancient evolutionary lineage (Byun, 1999; Fleming, pers. com.)

Two important inferences arise as a result of this recent genetic work. First, there may be a second population of QCI ermine located in Southeast Alaska across Dixon Entrance from Graham Island. The mtDNA cytochrome b gene in 8 specimens from the Prince of Wales Island group is identical to that in the one fresh specimen available to date from Haida Gwaii, and very similar to two other Haida Gwaii specimens from museum skins (Fleming, pers. com.; Byun, 1999). This genetic data suggests that ermine from Haida Gwaii and those from the Prince of Wales Island group share both common ancestry and a small source population (M. Fleming, pers. comm.). A second mtDNA gene, the so called d-loop, differs between the one fresh specimen from Haida Gwaii and those from Prince of Wales Island in only one base pair out of 305 in the sequence. This relatively small difference is thought to reflect divergence between the two populations since the last glaciation (M. Fleming, pers. comm.). Apparently, ermine in Haida Gwaii and the Prince of Wales Island group may have persisted in the same coastal refugium during the last glaciation, perhaps, as hypothesized by Byun (1999), on terrain now inundated under Hecate Strait.

The second inference from this recent work is that ermine found in Haida Gwaii and the Prince of Wales group are the only known representatives of one of only three or four ancient evolutionary lineages in M. erminea. The degree of genetic divergence between the QCI lineage and the others is consistent with separation considerably more ancient than the most recent glaciation, but current understanding of mutation rates does not permit precise dating (M. Fleming, pers. comm.). Separation of these lineages is also apparent anatomically. Hall (1951) argued on anatomical grounds that the QCI ermine is more deserving of species status than is any other subspecies of M. erminea. Eger’s (1989) analysis of skull size and shape in ermine closely parallels recent genetic data. Ermine skulls from Queen Charlotte Islands and the Prince of Wales group are similar to one another, but different from skulls from all other locations sampled.

All this suggests that, in its own right, the QCI ermine may warrant consideration close to that appropriate for a separate species, and certainly deserves more consideration than other individual subspecies of M. erminea would deserve in similar circumstances.

In North America, the QCI ermine is intermediate in size between the larger long-tailed weasel (M. frenata) and the smaller least weasel (M. nivalis). In addition to size differences, these three North American weasels are also distinguished by relative tail length which is longest in the long-tailed weasel, intermediate in the short-tailed weasel, and shortest in the least weasel. The long-tailed weasel and the short-tailed weasel, but not the least weasel, have prominent black tips on their tails (Fagerstone, 1987). These black tips seem likely to serve to confuse attacking predators (Powell, 1982).

The QCI ermine moults to a white coat during winter. Ironically, since snow cover is relatively infrequent at low elevations in Haida Gwaii (Reid et. al., 2000; Banner et. al., 1989) white winter pelage may not be an advantage there. Winter coat colour in other populations of short-tailed weasels varies roughly according to climate, with white coloration occurring in areas with cold temperatures and persistent winter snow, brown coloration occurring in warmer climate, and intermediate coloration sometimes occurring in intermediate climate (King, 1990).

Like other subspecies of the short-tailed weasel, the QCI ermine is sexually dimorphic, with male skulls being about 1.29 times the mass of female skulls (Foster, 1965). Virtually all other North American subspecies are more dimorphic, with male skulls ranging from 1.42 (Washington and Oregon coast) to 1.57 (Alaska) times the mass of female skulls (Foster, 1965). One exception to this pattern is M. e. anguinae on Vancouver Island in which male skulls are 1.25 times the mass of female skulls, dimorphism more or less similar to that found in the QCI ermine. Dimorphism in overall body weight is probably slightly greater than is indicated by Foster’s data on skull mass, because in both marten and ermine, dimorphism of skull size is less than dimorphism of body size (Holmes and Powell, 1994).

The reduced dimorphism in QCI ermine, and perhaps Vancouver Island ermine, may arise from poorer nutrition, less intense sexual selection for large male size, or perhaps both. Sexual dimorphism in fisher has been shown to be greater as a result of larger size of males when better nutrition is available (Powell 1994), so it is possible that the relatively low dimorphism in the QCI ermine and Vancouver Island ermine simply reflects the relatively depauperate rodent prey supply found in both locations.

Further, sexual selection in both these island populations may be different than it is elsewhere. Given the relatively poor prey base in both places, it is possible that distribution of female ermine is atypical in a way that reduces the competitive advantage of large male size. If, for example, female ermine have very large territories or are transient due to scarce prey (see Powell, 1994; Debrot, 1983; and Alterio, 1998) males might encounter one another less often, and the advantage of size in obtaining access to females might be reduced.

Descriptions of known specimens of the QCI ermine are summarized in Appendix 1.

The QCI ermine is commonly considered to be found only in Haida Gwaii, off the north central coast of British Columbia (Hall, 1951; Foster, 1965; Cowan, 1989; Reid et. al., 2000). This archipelago consists of two large islands, Graham Island in the north, and Moresby Island in the south, and many small and intermediate sized islands. Recent inventory attempts (Reid et. al., 2000) indicate that the subspecies is probably intermittently present in widespread locations at least on Graham, Moresby, Louise, and Burnaby Islands (Figure 1). The areas of these and other major islands, and the distances from them to other land is listed in Table 1.

As discussed earlier in this review, DNA and anatomical evidence suggest that ermine in Haida Gwaii are the same evolutionary lineage as those found in the Prince of Wales Island group in nearby Southeast Alaska (Figure 2). At minimum, recent analysis demonstrates that these two ermine populations are far more closely related to one another than either is to any other subspecies of the short-tailed weasel. Consequently, the QCI ermine may arguably include at least two separate populations, one in Haida Gwaii, and the other in the Prince of Wales Island group in Southeast Alaska. The population in Haida Gwaii may be fragmented into three sub-populations on Graham, Moresby/Burnaby, and Louise Islands due to the water distance between them. It is also possible that ermine exist on a few other major islands such as Langara, Lyell, and Kunghit, but have not been detected.

Table 1: Occupation of Canadian islands by QCI ermine
Island Known to be Occupied? Area Nearest land Distance to nearest land
Graham Yes 6389 sq. km Moresby Island 0.25 km
Moresby Yes 2549 sq. km Graham Island 0.25 km
Louise Yes 272 sq. km Moresby Island 0.10 km
Lyell No 175 sq. km Moresby Island 1.5 km
Kunghit No 130 sq. km Moresby Island 0.86 km
Burnaby Yes 66 sq. km Moresby Island <<0.10 km (possibly drying at lowest tides)
Langara No 33 sq. km Graham Island 1.1 km

Total area of Canadian islands confirmed as occupied - 9276 sq. km

Until and unless further sampling confirms otherwise, it would be prudent to assume that the QCI ermine occurs in Canada only in Haida Gwaii and, arguably, in Alaska in the Prince of Wales Island group.

Reid et. al. (2000) analyzed available records of trapped ermine, or of observed ermine or ermine sign, to try to identify habitat preferences of the Queen Charlotte Islands (QCI) ermine. Their data is presented in Appendices Most of their records (93%) were from the CWHwh1, the biogeoclimatic variant covering most of the eastern side of Haida Gwaii below about 350 m in elevation. Less than 2% were from higher elevations in the CWHwh2 on the eastern side of Haida Gwaii, and less than 5% from the CWHvh2 on the western side of Haida Gwaii.


Figure 1: QCI ermine records

Figure 1. QCI ermine records.

Data from Reid et.al., 2000.


Eighty seven percent of their records were from forested habitats – 69% from coniferous forest, 9% from mixed coniferous-deciduous forest, 7% from forested bog, and 1% each from deciduous forest and shrub. Of these records from forested habitats, 48% were in uncut forest, 37% in clearcuts over 10 years old, and 14% in clearcuts less than 10 years old.

An additional 13% of records were associated with unforested habitats, including 5% from beaches, 4% from pasture, and 4% from fens.

Combined, the above results mean that some 57% of records were from either unforested habitats or from second growth forests. Only 42%Footnote 5 were from uncut forest, and not all that was necessarily old growth.

One hundred and seventeen records included data on distance to the nearest water body, usually the ocean, a creek or a river. Seventy seven percent of these records were within 100m of water. There was a tendency for records to be closer to the ocean, an estuary, a river, or a creek than to a lake or marsh.

Reasonably accurate elevations were available for 73 records. Of these, 64% were within 10m of sea level. These records included all those from beaches and pastures, and 60% of the records from forested habitat of known elevation. Twenty three percent of the 73 records were from 11 to 50m elevation, and only 12% from >50m elevation. The highest record was from 800m on Slatechuck Mountain, still in forested habitat.


Figure 2: Distribution of QCI lineage

Figure 2. Distribution of QCI lineage.

Data from Reid et.al., 2000, and Fleming and Cook, 2000.


Reid et. al. (2000) also reported on two additional ermine that were recently trapped live. The first was taken from second growth riparian forest 47m from Sachs Creek about 700m from the ocean. The forest was dominated by Sitka spruce (10 to 109 cm dbh) with substantial components of western hemlock (31 to 52 cm dbh), and red alder (15 to 41 cm dbh). Canopy closure was 75 to 80% with little understory or forest floor vegetation. Substantial amounts of coarse woody debris were present (25% cover of pieces >5 cm diameter.). Black bears were actively feeding on spawning chum salmon (Oncorhynchus keta) in Sachs creek at the time the ermine was trapped.

The second ermine was trapped in upland second growth forest about 30-40 years old near mile one on South Main road. The forest was dominated by Sitka spruce (17 to 51 cm dbh), with substantial components of western hemlock (13 to 36 cm dbh), red cedar (14 to 48 cm dbh), and alder (15 cm dbh). Canopy closure was 70 to 80%, with a moderate cover of shrubs and ferns on the forest floor.

Interpretation of available ermine records is difficult. As Reid et. al. (2000) point out, apparent trends reflect not only the distribution of ermine, but also the distribution of potential observers. Further, even if distribution of observers were not a confounding factor, the analysis of the data would still suffer from lack of analysis of the availability of various habitat types.

The authors were aware of these limitations, however, better data are not available. Even with due consideration to limitations of their data, the authors argue that the results suggest three trends in habitat use by QCI ermine. First, their data indicate no particular reliance on old growth forests. Some 57% of their records were from non-forested habitats or second growth forests. Even given biased distribution of observers, and unknown availability of habitats, this result is extremely inconsistent with a preference or need for old growth forest habitat.

Second, the authors observe that records seem to be clustered, to a greater degree than seems reasonably explained by distribution of observers, in riparian and marine shoreline habitats.

Third, they suggest that the strong concentration of observations at low elevations is at least partly a reflection of habitat preference because an extensive network of higher elevation roads is present in Haida Gwaii, and should have resulted in more high elevation records if many ermine are found there.

In summary then, Reid et. al. (2000) concluded that QCI ermine are not particularly dependent on old growth forest, that they use a wide variety of habitats, and that they probably exhibit a preference for low elevation habitats near water bodies, especially the ocean, rivers, creeks and estuaries.

These conclusions are consistent with observations of short-tailed weasels elsewhere. Short-tailed weasels exploit very diverse habitats, which in North America range from eastern deciduous forests through prairie and arctic tundra to boreal and montane forest, and in Europe include many successional habitats including forest edges, wet meadows, ditches, riparian woodlands, and riverbanks (Fagerstone (1987), Banfield (1974), Cowan and Guiguet (1965), Lisgo (1999), Samson and Raymond (1998), Doyle (1990), Sullivan and Sullivan (1980), Simms (1979b), Fitzgerald (1977), MacLean et. al. (1974), Maher (1967), and Aldous and Manweiler (1942)).

It is safe to assume that QCI ermine will use whatever habitats provide sufficient prey, and tolerable risk of predation. The apparent habitat preferences observed by Reid et. al. (2000) probably reflect better food supply, lower predation risk, or a combination of both.

General biology of the Queen Charlotte Islands (QCI) ermine has not been studied directly, but much can be reasonably extrapolated from knowledge of other subspecies of the short-tailed weasel.

Breeding in other ermine subspecies takes place in spring shortly after parturition. If a female is not impregnated, oestrus may continue until fall. After impregnation, implantation is delayed until it occurs in spring in response to increasing day length (Fagerstone, 1987).

Other ermine subspecies have only one litter per year; litter size ranges from 4 to 13 young per litter, and averages 6 (Fagerstone, 1987). Both short-tailed weasels and least weasels produce more young during prey abundance than during prey scarcity, and are unable to reproduce at very low prey densities (Erlinge, 1983; King, 1985; Jedrzejewski et. al., 1998; Korpimaki et. al., 1991). Given the relatively poor prey base available (about which more later) to QCI ermine, mean litter size and juvenile production in this subspecies probably fall in the lower part of ranges observed elsewhere.

Annual survival in other subspecies of short-tailed weasel is around 40%, and average life expectancy about 1 to 1.5 years (Fagerstone, 1987). Quantitative descriptions of the causes of mortality in short-tailed weasels are not available, but predation appears important. It seems reasonable to assume that the QCI ermine is vulnerable to predation, particularly by marten. Reid et. al. (2000) documented predation of QCI ermine by domestic cats. QCI ermine may also be taken occasionally by black bear and raccoon. As Northern GoshawkFootnote 6, Bald Eagle, and Red-tailed Hawk are regularly recorded on Haida Gwaii, and the latter two species are recorded as breeding there (Campbell et. al., 1990), and as all these species may be assumed capable of taking ermine (Kaufman, 1996), these avian predators may also be a risk to QCI ermine. Predation, particularly by marten, will be discussed in detail later in this report.

Home ranges of female ermine typically overlap considerably with home ranges of males, but to a much smaller degree with those of other females. Male home ranges typically overlap with more than one female home range, but overlap little with other males’ home ranges. Ermine probably exclude other ermine of the same sex more by mutual avoidance through olfactory or acoustic signals than by overt aggression or fighting. However fighting among males may be more common during the breeding season than at other times of the year (Fagerstone, 1987, Simms, 1979a; Simms, 1979b).

Home range size has varied substantially in studies of ermine in North America. Home ranges of female ermine averaged 80ha in Alberta (Lisgo, 1999), 10-15 ha in Ontario (Simms, 1979b), and 3.5-7 ha in California (Fitzgerald, 1977). Male home ranges in these studies were roughly twice the size of female ranges. Home range size in stoats (Erlinge, 1983) and Eurasian least weasels (Jedrzejewski et. al. 1995) has been observed to increase in apparent response to prey scarcity.

Given the relatively depauperate prey base in Haida Gwaii, home ranges of QCI ermine can be expected to be relatively large. Experience with stoats introduced to New Zealand may be instructive here. Introduced house mouse (Mus musculus) and black rat (Rattusrattus) are the only small mammals available to stoats in New Zealand, a situation somewhat analogous to circumstances in Haida Gwaii. During shortages of these rodents, stoat home ranges are very large, averaging 223 ha for males, and 94 ha for females, and include extensive overlap both within and between sexes (Alterio, 1998). Similar overlap of home ranges has also been observed among stoats in Switzerland during shortages of the preferred water vole, even when another species of vole was available as prey (Debrot, 1983). The stoat in New Zealand originated in Britain (Alterio, 1998), and consequently is considerably larger than the QCI ermine, so home ranges in Haida Gwaii may be somewhat smaller. On the other hand, home ranges in Haida Gwaii seem unlikely to be smaller than those observed in Alberta by Lisgo (1999) where arvicoline rodents are present. For the purposes of present discussion, home ranges of ermine in Haida Gwaii can be assumed to be on the order of 100 ha for females and perhaps as much as 150 – 200 ha for males. Considerable overlap of home ranges both within and between sexes is likely.

Virtually no data on food habits of QCI ermine are available, so the likely diet of this sub-species must be surmised from habits of weasels elsewhere and information on availability of potential prey in Haida Gwaii.

Hunting behaviour of weasels is described by King (1985). They hunt very actively, zigzagging extensively over the habitat being hunted, checking every hole or crevice that may be occupied by prey. Prey is located more by sight and sound than by smell. Attack and killing behaviour is instinctive and triggered by sight, especially if prey is moving. Killing occurs whether or not the weasel is hungry, and excess prey killed is often cached for potential use later.

Given this behaviour, it is not surprising that ermine take a wide variety of prey. Ermine studied elsewhere feed primarily on small mammals, but also take birds, reptiles, fish, amphibians, and insects and other invertebrates (Fagerstone, 1987). This wide variety notwithstanding, ermine are primarily specialized predators of arvicoline rodents (voles and lemmings), with female ermine specifically sized to allow entrance to subnivean or subterranean burrows of important species of arvicoline prey (Fagerstone, 1987; Simms, 1979a). The primary reason for the difference in size between stoats and ermine seems likely to be the presence of the large water vole (Arvicola terrestris) throughout Europe. This large vole does not occur in North America, and ermine there are smaller to match the smaller voles available to them (Simms, 1979a).

Arvicoline rodents are not present in Haida Gwaii. The only native small mammals available as prey to the QCI ermine are Keen’s mouse (Peromyscus keeni) and dusky shrew (Sorex monticolus) (Cowan, 1989; Nagorsen, pers. comm.) It seems likely given typical hunting behaviour of short-tailed weasels that both of these small mammals will, wherever they are common or abundant, be important in QCI ermine diets. Red squirrels (Tamiasciurus hudsonicus), black rats, Norway rats (Rattus norvegicus) and muskrats (Ondatra zibethica) have been introduced to Haida Gwaii (Bertram and Nagorsen, 1995; Cowan, 1989). Red squirrels may presumably be taken by male QCI ermine, especially when naïve juveniles are available. In Alberta, red squirrels form a major part of the diet of male ermine (Lisgo, 1999). However, male ermine in Alberta average over 150g winter weight; n=10; Lisgo, 1999) and those in Haida Gwaii weigh only about 110g (n=4; Appendix 1) so male QCI ermine might be less successful than their Alberta counterparts in preying on squirrels. Male QCI ermine may have less success preying on roof rats which are larger than red squirrels, and even less on Norway rats which are larger still, or on muskrats which are both larger and presumably less often available due to their aquatic habits (Banfield, 1974).

Introduced squirrels, rats and muskrats are less likely to be killed by female QCI ermine than they may be by males. Female ermine in Alberta rarely took red squirrels (once in 97 female food records; Lisgo, 1999), presumably due in large part to relative size. Female ermine in Lisgo’s study averaged only 52g winter weight (n=9; Lisgo, 1999), and red squirrels averaged over 230 g, well over four times the size of the female ermine. It seems likely that the female ermine in Lisgo’s study would have taken more squirrels if they were capable of doing so. Small mammal densities were low and declining at the time of the study, and female home ranges were correspondingly large by North American standards.

It seems probable that birds form an important component of the QCI ermine diet, particularly species that spend considerable time on or near the ground such as, for example, Winter Wren, Dark-eyed Junco, Pine Siskin, American Robin, and Fox, Song, and Lincoln’s Sparrows. Diets of stoats introduced to New Zealand, where arvicoline prey are absent, are dominated by birds (King and Moody, 1982). Birds also form a major part of the non-arvicoline portion of ermine diets in Alberta (Lisgo, 1999), and birds were the single most important food group used by QCI marten during winter (Nagorsen et. al., 1991).

Potential prey species for QCI ermine are identified in Table 2.

Table 2: Potential prey species for QCI ermineFootnote a (Birds)
Year round residents/breeders Summer residents/breeders Migrants Mammals
Winter Wren Fox Sparrow Rock Sandpiper Dusky Shrew
Chestnut-backed Chickadee Song Sparrow Pectoral Sandpiper Keen’s Mouse
American Dipper Lincoln’s Sparrow Western Sandpiper Red Squirrel
Dark-eyed Junco Swainson’s Thrush Sanderling
Pine Siskin Hermit Thrush Surfbird
European Starling Pigeon Guillemot Black Turnstone
Northern Flicker Common Snipe Whimbrel
Black Oystercatcher Short-billed Dowitcher Long-billed Dowitcher
Steller’s Jay Semipalmated Plover Dunlin
Northwestern Crow Killdeer Wandering Tattler
Varied Thrush Spotted Sandpiper Greater Yellowlegs
American Robin Least Sandpiper Lesser Yellowlegs


Predation by ermine on most of the species is Table 2 is hypothetical, based merely on size and likelihood of spending time on the ground. Behaviour of many species, or the habitats typically occupied by them, may render them difficult or impossible for ermine to capture. Flocking shorebirds, for example, may be more or less impossible for ermine to catch due to their flocking behaviour and the open shoreline habitat they typically occupy. Nonetheless, Table 2 shows that, although the small mammal community in Haida Gwaii is depauperate, the community of potential bird prey is not. Given the demonstrated use of bird prey by short-tailed weasels elsewhere even when more preferred arvicoline prey species are available (Lisgo, 1999; Fagerstone, 1987; Fitzgerald, 1977, Simms, 1977b), and the dominance of birds in diet of New Zealand stoats which suffer from an absence of arvicolines (King and Moody, 1982), it is reasonable to expect ermine in Haida Gwaii to make significant use of birds.

Potential importance of birds to ermine in this coastal ecosystem is also supported by the fact that birds were the most important food group for marten in Haida Gwaii in winter when many species of potential bird prey are not present (Nagorsen et. al. 1991). The 29% by volume contribution of birds to marten diets in Nagorsen et. al. (1991) may be an overestimate due to bias caused by visibility of feathers in carnivore scats (see Buskirk and MacDonald, 1984; Martin, 1994). Nonetheless, the unusual importance of birds in QCI marten diets stands, and may suggest a similar importance of birds for QCI ermine.

QCI ermine can also be expected to scavenge. This behaviour has been documented by observations reported by Reid et. al. (2000), and is suggested if not proven by success in capturing QCI ermine in traps baited with meat (Hughan, pers. comm.). Again, food habits of QCI marten may be somewhat instructive here. Scavenged black-tailed deer formed over 15% by volume of identified, non-bait foods in winter marten diet in Haida Gwaii, and over 14% on Vancouver Island (Nagorsen et. al., 1989; Nagorsen et. al., 1991). It would not make sense for QCI ermine to ignore this source of food, other perhaps than in order to avoid marten, about which more later. Ermine can also be expected to scavenge salmon carcasses, or parts of carcasses left by other carnivores, during spawning season.

QCI ermine may also prey on intertidal animals such as crabs, and no doubt they scavenge on various animal parts that float to shore along intertidal areas.

As mentioned earlier, the evolutionary lineage to which the Queen Charlotte Islands (QCI) ermine belongs is one of three or perhaps four ancient lineages found in M. erminea. The QCI lineage has to date been found only in Haida Gwaii and on the nearby Prince of Wales Island group. The population in Haida Gwaii is the only one known to exist in Canada.

Additional genetic evidence suggests that ermine populations in Haida Gwaii may be especially important in representing this QCI lineage. Microsatellite DNA suggests that the Prince of Wales population has been influenced by male invasion from the nearby mainland (M. Fleming, unpubl. data). Although no female invasion has been detected yet, the fact that males have successfully colonized the area suggests that it may only be a matter of time until females arrive. It is also possible that females have already arrived but not been detected. In any case, it seems that the Haida Gwaii population may be the only remaining “pure” representative of the original QCI lineage, and it is certainly the only known population of this lineage not threatened with immigration of other subspecies. In any case, it is the only known population of this lineage in Canada.

The relative uniqueness of the QCI ermine itself is not the complete picture. The QCI ermine is part of a depauperate endemic fauna widely recognized as very special in the study of biogeography and evolution in North America (Cowan, 1989; Byun, 1999). The QCI ermine’s place in this unique fauna arguably lends the continued survival of this subspecies greater importance than would otherwise be the case.

Reid et. al. (in press) reported on several recent attempts to inventory this subspecies. Over 6700 trap-nights with baited live traps from 1992 and 1997 resulted in only 2 ermine captured. Further, some 2700 tracking station nights, and many kilometres of snow tracking (22 on foot, 900 km from a vehicle) failed to locate definite ermine sign in 1997 and 1998. Although the possibility still exists that different trapping techniques might have resulted in more ermine captured, Reid et. al. (2000) on balance believe that their results demonstrate that this subspecies is currently very rare in Haida Gwaii.

Trends over time in the numbers of observed or trapped ermine reported by Reid et. al. are not clear, although fewer records in the 1950’s and 1960’s in comparison with earlier and later decades might reflect changes in population size.

The only other indirect evidence of population trends available to this update is the fact that early collectors seem to have had higher trapping success, perhaps dramatically higher, than more recent trapping attempts have had. Four specimens, 2 of which were apparently taken on the same day, are attributed to W.H. Osgood over a one month period in 1900; 3 are attributed to W.W. Brown over a two week period in 1914; 4 are attributed to J.A. Munro in 1917 and 1918; and 4 were attributed to A. Brooks in May, 1920 (Appendix 1). Although details of their trapping effort are unknown, it seems unlikely that these collectors undertook anywhere near the trapping effort recently reported by Reid et. al. (2000), particularly not effort specifically targeting ermine. At least W.H. Osgood and J.A. Munro, and most likely the other collectors as well, were engaged in broad sampling of small mammals (Nagorsen, pers. comm.). Consequently, early collection data suggests that ermine were more common, perhaps much more common, in the early 1900’s than they are now.

Availability of particular habitats is very unlikely to be a limiting factor for the Queen Charlotte Islands (QCI) ermine. The short tailed weasel is highly plastic in its use of different habitat types, and readily uses numerous types of seral associations and unforested areas (Fagerstone (1987), Banfield (1974), Cowan and Guiguet (1965), Lisgo (1999), Samson and Raymond (1998), Doyle (1990), Sullivan and Sullivan (1980), Simms (1979b), Fitzgerald (1977), MacLean et. al. (1974), Maher (1967), and Aldous and Manweiler (1942).

Three other potential limiting factors deserve detailed attention here, namely food availability, interactions with marten, and interactions with other introduced species.

Short-tailed weasels are specialized predators superbly adapted to locating and killing arvicoline mammals. Female short-tailed weasels are just small enough to permit them to enter subnivean and subterranean burrows, and, over the geographic range of this species, size of females is correlated closely with the size of locally important species of arvicoline prey (Simms, 1979a). The short tailed weasel’s ability to enter burrows means that prey have no physical refuge in which to escape, and means that weasels can effectively hunt both adult and juvenile prey at any time of the day or year, independent of the activity of prey.

Ermine diets are strongly dominated by arvicoline rodents, especially Microtus spp., Clethrionomys spp., Lemmus spp. and Dicrostonyx spp. (Lisgo, 1999; Fagerstone, 1987; Simms, 1979a; Fitzgerald, 1977; Aldous and Manweiler, 1942). Stoat diets are also dominated by arvicolines, especially Arvicola spp., Microtus spp., and Clethrionomys spp. (Erlinge, 1981; Debrot, 1983; King, 1985; Korpimaki et. al., 1991). Diets of Eurasian least weasels, which are roughly similar in size to ermine, are also dominated by arvicolines, especially Microtus spp. and Clethrionomys spp. (Jedrzejewski et. al. 1995; Korpimaki et. al., 1991; King, 1980).

Various studies have demonstrated a link between densities of prey and densities of short-tailed and least weasels (Alterio, 1998 and references therein; Jedrzejewski et. al. 1995; Korpimaki et. al., 1991; King, 1985 and references therein; Fitzgerald, 1977). When prey (usually arvicolines) are abundant, weasel reproduction or, more accurately, inferred reproduction, is more successful, and weasel populations grow; when prey are scarce, reproduction slows or fails, and weasel populations decline or disappear.

Arvicolines are absent from Haida Gwaii. Consequently, potential small mammal prey in Haida Gwaii, at least for female ermine, is probably limited more or less exclusively to Keen’s mice and dusky shrews. Both Peromyscus maniculatus and dusky shrews have been documented in short-tailed weasel diets elsewhere in North America (Lisgo, 1999; Simms, 1979a; Fitzgerald, 1977). In these three studies, shrews were more common in weasel diets than P. maniculatus were. As mentioned earlier, introduced squirrels, rats, and muskrats are probably of little use to female ermine, and consequently the food resources they provide probably play a limited role in the population dynamics of QCI ermine.

Given the apparent dependence of short-tailed weasels on small mammals elsewhere, especially the frequent dependence on arvicolines, the depauperate small mammal community present in Haida Gwaii would appear to be a potentially serious disadvantage for the QCI ermine. Deer mice may be more difficult to catch than the arvicolines for which the ermine seems best adapted (King, 1985), and several studies suggest avoidance of deer mice in diet selection by ermine (Lisgo, 1999; Simms, 1979b), and marten (Thompson and Colgan, 1990; Weckworth and Hawley, 1962) perhaps for this reason. As Keen’s mouse is more arboreal than deer mice are (Nagorsen, pers. com.), it may be even less vulnerable to ermine predation. Mean body mass of the dusky shrew is about 6 g (Nagorsen 1996) so they may be a poor substitute for the larger arvicoline prey for which the ermine is adapted.

There is no question that the combination of prey available to QCI ermine is different that that available to short-tailed weasels elsewhere, and is probably not what ermine are best adapted to exploit. However, the more relevant question here is whether the dramatically different food resources available for QCI ermine impose unusual constraints for its continued survival, and if so, what if anything can be done to improve the situation? The odd mix of foods available to QCI ermine has certainly been sufficient to enable ermine to persist until now, but recent food supply may have changed, not least because of the various influences of introduced species. Unfortunately, there is no way of knowing how adequate historic food supply was, or of knowing the degree to which it has changed in response to human influences over the last century.

On balance, it is probably fair to assume that food supply for QCI ermine has always been relatively poor in comparison to locations where a more normal complement of arvicoline rodents is available, and that this relatively poor food supply may have always limited QCI ermine to relatively low densities. Whether food supply is much different today is uncertain.

Important interactions between QCI ermine and American marten may include both competition for food, and predation of ermine by marten. The magnitude of the problem presented for ermine by both these interactions may have been worsened by recent increases in marten populations. Evidence for increased marten populations, for competition between marten and ermine for food, and for predation of ermine by marten are discussed separately below.

No trend data on QCI marten populations have been located during this review. However, anecdotal evidence strongly suggests that marten populations have increased dramatically in recent decades. Reid et. al. (2000) found general agreement among interviewed trappers that marten populations in Haida Gwaii have increased by a factor of between five and ten since the 1940s. Given trappers’ unanimous agreement on an increase this large, it is clear that marten populations must be dramatically higher now than they were in the 1940’s.

Deer were introduced to Haida Gwaii prior to 1912 (Banfield, 1974). Given the significant role of deer carrion in at least winter diets of QCI marten, marten populations may have already increased by the time available trapper observations began. If so, the 5x to 10x increase in marten populations suggested by trappers could be an underestimate.

Further to interview results reported by Reid et. al. (2000), H. Hughan (pers. comm.), who has trapped marten for several recent years on both Haida Gwaii and the B.C. mainland, considers recent marten populations in Haida Gwaii to be unusually high in comparison with good mainland habitats.

Although trends in trapping effort cannot be ruled out, it seems probable that the reason for the increase in marten populations has been the introduction of new food species, especially black-tailed deer, red squirrel, black rat and Norway rat. Collectively, these introduced mammals contributed over 23% by volume of identified foods other than bait in diets of QCI marten (Nagorsen et. al., 1991). In the winter season sampled, deer carrion was the largest contributor at over 15% (although some of this may have been bait; Nagorsen, pers. com.); muskrat followed at over 4%, red squirrel at 3%, and rat at 1%. Keen’s mouse was the only native mammal documented in marten diet, and contributed only 3% by volume of identified, non-bait foods. It is possible that introduced species may be even more important in other seasons. This may be particularly true of the three rodent species when naïve juveniles become available in summer. Elsewhere, marten have been observed to kill more sciurids in spring and summer (Zielinski et. al., 1983; Weckworth and Hawley, 1962), possibly at least partly because naïve animals are available then. Although introduced American beaver (Castor canadensis) and elk (Cervus elaphus) (Cowan, 1989) were not documented as marten food by Nagorsen et. al. (1991), they may provide locally important carrion sources as well.

The hypothesis that competition between marten and ermine exists would be strengthened if both predators occupy the same habitats, and if both exploit the same foods.

Detailed information on habitat use by marten in Haida Gwaii is not available. However, work elsewhere suggests that, in general, marten can be expected to use whatever late successional forest habitats provide food (Buskirk and Powell, 1994). Whether marten in Haida Gwaii need the structural complexity often preferred elsewhere is uncertain because potential marten predators are fewer in Haida Gwaii, and access to subnivean spaces may be less important given the infrequent snow cover in Haida Gwaii. It is probably safe to assume that habitat overlap between marten and ermine occurs at least in most late successional forests used by ermine, and it may occur elsewhere as well given the relatively snow-free climate of Haida Gwaii.

Other evidence also supports overlap in use of habitat. Cowan (1989) states that marten commonly use marine shorelines for foraging, a habitat in which early collectors were particularly successful in trapping ermine (Osgood, 1901). H. Hughan has probably trapped more QCI ermine in recent years than anyone has for many decades (Appendix 2). All of them were captured in late successional forest near the Yakoun River in traps set for marten, the same traps in which he also caught some 60-100 marten each winter.

There is good reason to believe that marten diets have always overlapped with diets of QCI ermine. Even now when most mammal food taken by marten in winter is derived from introduced species, Keen’s mouse still contributes by volume over 3% of all identified foods, and over 11% of identified mammal foods (Nagorsen et. al., 1991). Before introduction of exotics to Haida Gwaii, Keen’s mouse would have been the only mammal prey available to marten other than shrews, and present winter food habits (Nagorsen et. al., 1991) suggest that shrews were not likely prominent in historic marten diet. As mentioned earlier, it seems likely that Keen’s mouse was historically and is now very important in QCI ermine diet.

Historical food supply was probably a serious limitation for both marten and QCI ermine given the lack of native small mammals. It seems reasonable to expect that Keen’s mouse was important prey to both predators, but especially to ermine, and that exploitative and interference competition may have occurred as a result. However, whether either type of competition actually existed historically is not determinable. If Keen’s mouse were sufficiently abundant, or were sufficiently proficient in avoiding marten and ermine, or if habitats actually hunted by marten and ermine tended to be separate, dietary and geographic overlap may not in themselves have resulted in competition. In any case, historical competition for Keen’s mouse may have been more of a problem for marten than for ermine. Ermine may be a more efficient predator of Keen’s mouse due to their ability to enter smaller potential escape refuges than marten can enter, and due to smaller body size of ermine and the consequent smaller energy expenditure necessary to catch and kill a mouse. Generally, evidence suggests that the smaller of sympatric mustelids will be the more formidable competitor for the small prey species it regularly kills (Rosenzweig, 1966; Simms, 1979a).

Whether competition over Keen’s mouse, if it originally existed, has become worse or better for the ermine as a result of introduced species is moot. On the one hand, marten now have new food sources which may have reduced marten reliance on mice. On the other hand, there are apparently far more marten in Haida Gwaii now than there once were, so even if fewer mice are now taken per marten, far more mice may be taken in total. Data do not exist to determine the relative magnitude of these two influences.

Competition for other prey species, perhaps most notably birds, may also have existed historically, and may have changed as a result of increasing marten populations. Argument here is similar to that for deer mice, but even more speculative and inconclusive.

Competition for carrion could be an important issue for ermine. As noted earlier, carrion is used to an apparently important degree by marten, and ermine can be expected to use carrion as well. Marten can be expected to appropriate and remain in the vicinity of attractive carrion until it is exhausted (Lensink et. al., 1955), thereby directly depriving ermine of access, and/or subjecting ermine attracted to such carrion to unusually high predation risk. This problem for ermine would presumably have increased greatly as a result of increased marten populations.

In summary, the role of food competition in interactions between marten and ermine is not clear. It seems likely that both exploitative and interference competition for carrion has increased to the detriment of ermine.

Weasels occur in the diets of numerous predators including coyotes, red fox, domestic cat, polecat, fisher, marten, long tailed weasel, short-tailed weasels and many hawks and owls (Reid et. al., in press; Jedrzejewski et. al. 1995; Weir, 1995; Mulder, 1990; Thomson and Colgan, 1990; Korpimaki and Nordahl, 1989; Fagerstone, 1987; Erlinge, 1983; Erlinge, 1981; Weckworth and Hawley, 1962; Latham, 1952; Gaughran, 1950; Polderboer et. al., 1941). Mulder (1990) provided compelling argument that predation by newly arrived foxes eliminated stoats from the coastal dune region of Netherlands, and Latham (1952) argued that irrupting fox populations in Pennsylvania substantially lowered weasel populations by predation.

Given the repeated documentation of predation of weasels by several mammalian predators, the apparent reduction of weasel populations by such predation in at least two instances, and the specific documentation of short-tailed weasels being predated by marten (Jedrzejewski et. al. 1995; Thompson and Colgan, 1990; Weckworth and Hawley, 1962) there is no doubt that individual QCI ermine are at risk of predation by marten.

There are also theoretical reasons to expect the larger of two sympatric mustelids to prey on the smaller (Rosenzweig, 1966). Put simply, the larger competitor can be expected to benefit from killing the smaller one whenever convenient because doing so will not only provide short term sustenance, it will increase long term fitness by reducing competition for other food.

Korpimaki and Nordahl (1989) argued that the potential importance of predation on short-tailed weasels has often been underestimated because investigators do not adequately consider the implications of diet composition data. Data presented by these authors suggest that even very small rates of occurrence of weasel in the diet of predators, on the order of 0.75%, can signal potentially significant impacts to weasel populations. Similarly, Powell (1973), using data from Craighead and Craighead (1956), constructed a mathematical model which he argued demonstrates that avian predators are capable of controlling weasel populations even when weasel occurs only at a roughly a 1% frequency in diet.

The argument made by Korpimaki and Nordahl (1989) and Powell (1973) is, in this author’s opinion, extremely important and warrants illustration. For example, consider a hypothetical marten which produces 700 scats per year. If that marten killed one ermine per year, only one scat in 700 would contain ermine, and a 0.14% FOC would result. If every marten in the population killed one ermine, an overall 0.14% FOC would still result. Put another way, a mere 0.14% FOC would imply that every marten would kill one ermine per year, i.e. that, given similar densities, as many ermine would be killed over a year as existed on day one. This hypothetical illustration assumes similar marten and ermine densities. It seems probable that marten densities in Haida Gwaii are now higher than ermine densities. It therefore seems highly unlikely that the relatively unproductive ermine populations in Haida Gwaii could sustain a 0.1% FOC in marten diets. In this context, it should come as no surprise that Nagorsen et. al. (1991) did not find ermine in diets of the 97 marten they analyzed. The likelihood of these authors detecting ermine in a sample of that size was probably less than one in ten, perhaps considerably less, even at predation levels that would probably be a threat to ermine.

As there is no doubt that QCI ermine are vulnerable to predation by marten, there is also no doubt that marten in Haida Gwaii find ermine very palatable. H. Hughan (pers. comm.) found that ermine caught in traps were invariably scavenged by marten if marten could reach them. The only reason Hughan obtained complete ermine carcasses as often as he did was that he always located traps on elevated logs so that trapped animals would hang clear of the ground, often out of reach of marten. Even though Hughan used this type of set exclusively, marten still managed to scavenge about half the ermine caught.

Marten are active hunters, and can be expected to opportunistically take whatever prey are encountered (Thompson and Colgan, 1990; Poole and Graf, 1996). This opportunistic predatory behaviour has very important implications for QCI ermine. Given the high palatability of QCI ermine to marten, and the documented vulnerability of short-tailed weasels to marten predation, this behaviour clearly suggests that marten probably take, or at least try to take, QCI ermine opportunistically whenever ermine are encountered. A rough corollary of this opportunistic behaviour is that the cumulative amount of predation on ermine has probably increased more or less in proportion to the increase in marten populations, i.e. there is good reason to believe that predation levels are probably several times higher, perhaps even an order of magnitude higher, now than they were historically. Given the relatively poor food supply available to QCI ermine, and the relatively low ermine productivity that probably results, such an increase in predation pressure might easily constitute a serious threat to the persistence of QCI ermine in many habitats, and perhaps in Haida Gwaii as a whole.

An anecdotal report from H. Hughan (pers. com.) is of potential interest here. Over several years, his normal harvest of ermine was from two to four animals. However, in one year he captured over 20 ermine, 13 of which were provided to the then Fish and Wildlife Branch, and the remainder of which were scavenged by marten. Effort and techniques were more or less constant. On questioning by the author of this report, Hughan recalled that, in one year during this time period, marten became very heavily infested with ticks, and his harvest of marten the following winter declined to something less than half of normal. He was unable to recall whether the reduction in marten harvest coincided with the increase in ermine harvest. Unfortunately, no data exist to clarify the timing of either the tick infestation or the increase in ermine harvest, and all or most of the 13 ermine provided to the Fish and Wildlife Branch appear to have been lost.

In summary, there is reason to believe that marten opportunistically kill and eat QCI ermine, and that increases in marten populations have probably resulted in more or less proportional increases in predation pressure. Although definitive data do not exist, this increase in predation may constitute a threat to the continued persistence of ermine in Haida Gwaii.

Introduced black rats apparently reduced populations of Keen’s mouse on Langara Island (Cowan, 1989), so both black and Norway rats may be capable of depressing mouse populations elsewhere. Other than potential impacts on Keen’s mouse, and provision of food for marten, interactions between rats and ermine seem unlikely to be important. Ermine may benefit from rat carrion, if they find it before marten do.

Interactions between ermine and introduced beaver, muskrat, and elk seem unlikely to be important except through provision of food to marten, and occasional provision of carrion to ermine.

Interactions between ermine and red squirrel might be significant. Red squirrel is the most carnivorous squirrel in North America (Banfield, 1974), and can be expected to take mice, small birds, nestlings, and eggs. Consequently, the possibility of both exploitative and interference competition with ermine exists. It seems unlikely that this competition would be as important as competition with marten, but it might be additive. Red squirrel may provide prey for male ermine, but seem unlikely to provide much other than carrion for females.

Interactions with black-tailed deer could also be significant as deer have virtually eliminated the shrub layer over widespread areas of Haida Gwaii (Banner et. al., 1989). It is possible that this removal of ground cover may make QCI ermine considerably more vulnerable to predation by both marten and birds such as Northern Goshawk, particularly in winter when white pelage makes ermine very visible due to lack of snow. As discussed earlier, deer provide important carrion for marten, and can be expected to do so for ermine, if the ermine get there first.

Interactions with raccoons could be significant as well. In particular, interference and exploitative competition over carrion, and possibly over intertidal invertebrates, seems possible along marine shorelines. Raccoons in Haida Gwaii preferentially use intertidal areas, largely in order to forage on intertidal invertebrates (Hartman, 1993). However, they can be expected to make use of carrion. Predation of ermine by raccoon is presumably possible, but seems unlikely to be common given the relative unimportance of mammals in raccoon diets (Johnson, 1970).

Of the various limiting factors considered in this review, predation by marten appears to this author as the most potentially damaging for QCI ermine. Effects of predation may be exacerbated by exploitative and interference competition, perhaps especially competition with marten for carrion.

Predation by marten and avian predators may have been exacerbated by introduced black-tailed deer which have removed the shrub layer in widespread areas of forests in Haida Gwaii and thereby caused widespread loss of vegetative cover for ermine. This loss of cover may be particularly important in winter when ermine are white and usually highly visible due to lack of snow.

This subspecies is classified as vulnerable by Committee on the Status of Endangered Wildlife in Canada (COSEWIC) (Youngman, 1984), and is on the Red List in British Columbia (B.C. Conservation Data Centre, 1999). Presence on the provincial Red List reflects imperilment both globally and provincially due to the subspecies’ apparent rarity and vulnerability to extinction. The current COSEWIC designation primarily reflects the above factors combined with the insufficient evidence available in 1984 to indicate jeopardy to the population.

Neither presence on the provincial Red List nor classification as vulnerable by COSEWIC affords the subspecies protection from mortality induced by humans through trapping or through other activity, or to detrimental effects caused by habitat change. While there is no open trapping season on Queen Charlotte Islands (QCI) ermine, this measure does not in fact prevent ermine from being accidentally caught in traps set for other species, particularly marten. However, the extremely low number of ermine taken by trappers in recent years (Reid et. al., 2000) is unlikely to have any impact on populations, nor would the small numbers that might be killed as nuisance animals, by pets, or for other reasons. Although this subspecies is not apparently dependent on old growth forest, the conversion of large tracts of forest to dense, closed-canopy second growth may significantly reduce the amount of useful habitat in the medium term.

Although this subspecies is not currently designated as an “Identified Species” under the Forest Practices Code (Province of B.C., 1999), it is possible that it will become designated in future, in which case special consideration may be given to it during forestry activities. It remains to be seen whether such designation is forthcoming, and whether resultant modifications to forestry activities, if any, prove beneficial to ermine.

Assessment of status of the QCI ermine is extremely difficult given the almost complete lack of direct data on the surviving population. Rigorous proof that the subspecies meets any of the current Committee on the Status of Endangered Wildlife in Canada (COSEWIC) criteria for Threatened or Endangered status is not possible with existing data, and is unlikely to be possible soon.

Applying quantitative criteria such as those used by COSEWIC for assigning status is difficult even when reasonable data exist, and is extremely difficult when faced with the degree of uncertainty surrounding the QCI ermine. The impact of uncertainty on use of such rule sets has been specifically discussed by Akcakaya et. al. (2000). The author proposes a decision process which would specifically incorporate uncertainty by using fuzzy numbers to reflect the degree to which particular criteria are likely met, or particular statements are likely true. This process is designed to in the end result not merely in a yes or no answer to each possible status, but rather in a best estimate of the most likely applicable status. Use of their process to evaluate the QCI ermine has not been undertaken here because applying it would probably involve canvassing several experts in the field, not simply relying on the author of this review. It would appear that the QCI ermine may be an excellent candidate for application of the process suggested by Akcakaya et. al. should COSEWIC be inclined to apply it.

There is little likelihood of useful new data becoming available. Ermine populations appear to be so thinly distributed now that direct study of them is probably no longer feasible unless densities can be increased by reduction of limiting influences. One way of clarifying the impact of marten predation comes readily to mind. Experimental removal of marten could be undertaken from a significant area of Haida Gwaii to see whether a population response from ermine results. It may behove interested government agencies to take steps in this direction while ermine are probably still present in numbers that can be detected if they respond. Success in such an experiment would at best only confirm the reason for decline, not cure it. It is highly unlikely that a widespread removal of marten for long term predator control would be feasible or politically acceptable.

On balance, it seems highly probable to this author that that increasing predation by marten, perhaps in conjunction with other influences, has caused a major decline in ermine populations since the early 1900’s, that this decline continues today as various impacts of introduced species continue to unfold, and that uninterrupted continuation of this process may eventually result in extirpation or near extirpation of ermine from Haida Gwaii. Recommendations of the author are:

  1. that the Queen Charlotte ermine receive threatened status, and
  2. that in light of recent genetic data, COSEWIC give the QCI ermine the priority normally afforded to separate species rather than subspecies.

Extent of occurrence: approximately 9500 sq km in Canada

Area of occupation: uncertain, but probably intermittently widespread at low density.

Total number of individuals in the Canadian population: unknown.

Number of mature individuals in the Canadian population: unknown.

Generation time: 1 year.

Population trend: uncertain, but probably declining.

Number of known populations: Two, if genetically related ermine in the Prince of Wales Island group in S.E. Alaska are Haidarum; one otherwise.

Is the total population fragmented? Yes, if ermine in S.E. Alaska are Haidarum. The Haida Gwaii population may be fragmented into three sub-populations due to distances between occupied islands.

Does the subspecies undergo fluctuations? Unknown; other subspecies do.

Primary limiting factors and threats appear to be:

Does subspecies exist outside Canada? Yes, if the population in the Prince of Wales Island group is Queen Charlotte Islands (QCI) ermine.

Is immigration known or possible? No, Dixon Entrance, which separates Haida Gwaii from the Prince of Wales Island group, is impassable to ermine.

Would individuals from the nearest foreign population be adapted to survive in Canada? Yes.

Would sufficient suitable habitat be available for immigrants? Yes, but habitat, as separate from predation risk and food supply, is probably not a limiting factor.

Very rare with low population numbers; likely declining.

Isolated from mainland ermine and populations on the southern Alexander Archipelago of Alaska with no possibility for rescue.

Population on Haida Gwaii fragmented into 3 subpopulations.

Marten populations on Haida Gwaii may have increased and impacted ermine through competition for prey and direct predation

The author gratefully acknowledges the kind assistance of several people during the preparation of this review: especially Donald Reid for arranging with his co-authors for access to their then unpublished manuscript on Queen Charlotte Islands (QCI) ermine, and for providing much helpful information and discussion throughout the project; Melissa Fleming for sharing her unpublished data on genetics of short-tailed weasel; Herb Hughan for spending time with me to document his experience with QCI ermine while he trapped in Haida Gwaii; and David Hatler for reminding me that Herb Hughan was by far the most successful known trapper of QCI ermine. Dave Nagorsen provided his historical museum records of M. e. haidarum and his data on island areas and isolation measures. The author is also grateful to David Nagorsen, Marco Festa-Bianchet, Jan Murie, Thomas Herman, Mark Brigham, and Michel Crete, all of whom reviewed an earlier draft of this report.

Funding for the preparation of this status report was provided by the Canadian Wildlife Service, Environment Canada.

Aldous, S.E. and J. Manweiler. 1942. The winter food habits of the short-tailed weasel in northern Minnesota. Journal of Mammalogy 23:250-255.

Alterio, N. 1998. Spring home range, spatial organization and activity or stoats Mustela erminea in a South Island Nothofagus forest, New Zealand. Ecography 21:18-24.

Akcakaya, H.R., A. Ferson, M.A. Burgman, D.A. Keith, G.M. Mace, and C.R. Todd. 2000. Making consistent IUCN classifications under uncertainty. Conservation Biology 14(4):1001-1013.

Banfield, A.W.F. 1974. The Mammals of Canada. University of Toronto Press. 438 pp.

Banner, A., W. Mackenzie, S. Haeussler, S. Thompson, J. Pojar, and R. Trowbridge. 1993. A Field Guide to Site Identification and Interpretation for the Prince Rupert Forest Region. Ministry of Forests, Victoria, B.C.

Banner, A., J. Pojar, J.W. Schwab, and R. Trowbridge. 1989. Vegetation and soils of Haida Gwaii: Recent impacts of development. Pp. 261-279 In The Outer Shores. G.G.E. Scudder and N. Gessler eds. Queen Charlotte Islands Museum Press. 327 pp.

Bertram, D.F., and D.W. Nagorsen. 1995. Introduced rats Rattus sp. on the Queen Charlotte Islands: implications for seabird conservation. Canadian Field-Naturalist 109:6-10.

B.C. Conservation Data Centre. 1999. (http://www.elp.gov.bc.ca/rib/wis/cdc/vertebrates.htm)

Buskirk, S.W. and R.A.Powell. 1994. Habitat ecology of fishers and American martens. Pp. 283-296 In Martens, Sables, and Fishers: Biology and Conservation. Buskirk S.W., A.S. Harestad, M.G.Raphael, and R.A.Powell. eds. Cornell University Press, Ithaca and London. 484 pp.

Buskirk, S.W., and S.O. Macdonald. 1984. Seasonal food habits of marten in south-central Alaska. Canadian Journal of Zoology 62:944-950.

Byun, S.A. 1999. Quaternary biogeography of western North America: Insights from mtDNA phylogeography of endemic vertebrates from Haida Gwaii. PhD Thesis. Univ. of Victoria, Victoria B.C. 280 pp.

Campbell R.W., N.K.Dawe, I.McT.Cowan, J.M.Cooper, G.W.Kaiser, and M.C.E. McNall. 1990. The Birds of British Columbia: Vols. 1& 2. Royal B.C. Museum, Canadian Wildlife Service. Victoria, B.C. 514pp. and 626 pp. resp.

Campbell, R.W., N.K. Dawe, I. McTaggart-Cowan, J.M. Cooper, G.W. Kaiser, M.C.E. McNall, and G.E.J. Smith. 1997. The Birds of British Columbia. Volume 3. 693 pp.

Campbell R.W., N.K. Dawe, I.McT.Cowan, J.M.Cooper, G.W.Kaiser, and M.C.E. McNall. 1990. The Birds of British Columbia: Vol. 2. Royal B.C. Museum, Canadian Wildlife Service. Victoria, B.C. 626 pp.

Cannings, R.A. and A.P. Harcombe. 1990. The Vertebrates of British Columbia: Scientific and English Names. Heritage record #20. Royal B.C. Museum, Victoria, B.C. 110 pp.

Cowan, I. McT. and C.J. Guiguet. 1965. The Mammals of British Columbia. Handbook No. 11. B.C. Provincial Museum, Victoria, B.C. 414 pp.

Cowan, I. McT. 1989. Birds and Mammals on the Queen Charlotte Islands. Pp. In The Outer Shores, Scudder G.E., and N. Gessler eds. Based on the proceedings of the Queen Charlotte Islands First International Scientific Symposium, University of British Columbia, August, 1984. Queen Charlotte Islands Museum Press. 327 pp.

Craighead, J.J., and F.C. Craighead. 1956. Hawks, owls and wildlife. Stackpole Co. and Wildlife Management Institute. 443 pp. (Referenced in Powell, 1973)

Debrot. S. 1983. The spatial and temporal distribution pattern of the stoat (Mustela erminea L.). Oecologia 59:69-73.

Doyle, A.T. 1990. Use of riparian and upland habitats by small mammals. Journal of Mammalogy 71:14-23.

Eger, J.L. 1990. Patterns of geographic variation in the skull of Nearctic Ermine (Mustela erminea). Canadian Journal of Zoology 68:1241-1249.

Erlinge, S. 1983. Demography and dynamics of a stoat Mustela erminea population in a diverse community of vertebrates. Journal of Animal Ecology 52:705-726.

Erlinge, S. 1981. Food preference, optimal diet and reproductive output in stoats Mustela erminea in Sweden. Oikos 36:306-315.

Fagerstone, K.A. 1987. Black-footed ferret, long-tailed weasel, short-tailed weasel, and least weasel. Pp. 549-573 In Wild Furbearer Management and Conservation in North America. M. Novak, J.A. Baker, M, E. Obbard, and B. Malloch eds. Ontario Ministry of Natural Resources, Toronto, Ontario.

Fleming, M., and J. A. Cook. 2000. Phylogeography of endemic ermine (Mustela erminea) in southeast Alaska. (unpublished manuscript submitted to Molecular Ecology).

Fitzgerald, B.M. 1977. Weasel predation on a cyclic population of the montane vole (Microtus montanus) in California. Journal of Animal Ecology 46:367-397.

Foster, J.B. 1965. Evolution of the mammals of Haida Gwaii, British Columbia. Occasional Papers of the British Columbia Museum #14. Victoria, B.C. 130 pp.

Gaughran, G.R. 1950. Domestic cat predation on short-tailed weasel. Journal of Mammalogy 31:356.

Hall, E.R. 1951. American Weasels. Publications. Museum of Natural History. University of Kansas 4:1-466.

Hartman, L.H. 1993. Ecology of coastal raccoons (Procyon lotor) on the Queen Charlotte Islands, British Columbia, and evaluation of their potential impact on native burrow nesting seabirds. M.Sc. Thesis. University of Victoria, Victoria, B.C.

Holmes, T, and R.A. Powell. 1994. Morphology, ecology, and the evolution of sexual dimorphism in North American Martes. Pp. 72-84 In Martens, Sables and Fishers: Biology and Conservation. Buskirk, S.W., A.S.Harestad, M.G. Raphael, and R.A. Powell, eds. 484 pp.

Jedrzejewski, W., Jedrzejewska, B., and Szymura L. 1995. Weasel predation response, home range, and predation on rodents in a deciduous forest in Poland. Ecology 76:179-195.

Johnson, A.S. 1970. Biology of the raccoon (Procyon lotor varius) Nelson and Goldman in Alabama. Auburn University Agricultural Experiment Station Bulletin No. 402. 148 pp. (Referenced in Hartman, 1993.)

Kaufman J. 1996. Lives of North American Birds. Houghton Mifflin Co., Boston and New York. 675 pp.

King, C.M. 1990. The Natural History of Weasels and Stoats. Cornell Univ. Press., New York. 253 pp.

King, C.M. 1985. Interactions between woodland rodents and their predators. Symposium of the Zoological Society of London 55:219-247.

King, C.M. 1980. Population biology of the weasel Mustela nivalis on British game estates. Holarctic Ecology 3:160:168.

King, C.M. and J.E. Moody. 1982. The biology of the stoat (Mustela erminea) in the National Parks of New Zealand II. Food habits. New Zealand Journal of Zoology 9:57-80. (referenced in Lisgo, 1999).

Korpimaki, E., K. Norrdahl, and T. Rinta-Jaskari. 1991. Responses of stoats and least weasels to fluctuating food abundances: is the low phase of the vole cycle due to mustelid predation? Oecologia 88:552-561.

Korpimaki, E., and K. Norrdahl. 1989. Avian predation on mustelids in Europe 1: occurrence and effects on body size variation and life traits. Oikos 55:205-215.

Latham, R.M. 1952. The fox as a factor in the control of weasel populations. Journal of Wildlife Management 16:516-517.

Lensink, C.J., R.O. Skoog and J.L. Buckley. 1955. Food habits of marten in interior Alaska and their significance. Journal of Wildlife Management 19:364-368.

Lisgo, K.A. 1999. Ecology of the short tailed weasel (Mustela erminea) in the mixedwood boreal forest of Alberta. M.Sc. Thesis. University of British Columbia, Vancouver, B.C. Canada.

MacLean, S.F. Jr., B.M. Fitzgerald, and F.A. Pitelka. 1974. Population cycles in Arctic lemmings: winter reproduction and predation by weasels. Arctic and Alpine Research 6:1-12. (Referenced in Lisgo, 1999).

Maher, W.J. 1967. Predation by weasels on a winter population of lemmings, Banks Island, Northwest Territories. Canadian Field-Naturalist 81:248-250. (Referenced in Lisgo, 1999).

Martin, S.K. 1994. Feeding ecology of American Marten and Fishers. Pp. 297-315 In Martens, Sables and Fishers: Biology and Conservation. Buskirk, S.W., A.S. Harestad, M.G. Raphael, and R.A. Powell, eds. 484 pp.

Mulder, J.L. 1990. The stoat Mustela erminea in the Dutch Dune Region, its local extinction, and a possible cause: the arrival of the fox Vulpes vulpes. Lutra 33(1):1-21.

Nagorsen, D.W., R. W. Campbell, and G.R. Giannico. 1991. Winter food habits of Marten, Martes americana in Haida Gwaii. Canadian Field Naturalist 105:55-59.

Nagorsen, D.W., K.F. Morrison, and J.E. Forsberg. 1989. Winter diet of Vancouver Island marten. Canadian Journal of Zoology 67:1394-1400.

Nagorsen, D. W. 1996. Opossums, Shrews and Moles of British Columbia. Royal British Columbia Museum handbook, University of British Columbia Press, Vancouver.

Osgood, W.H. 1901. Natural history of the Queen Charlotte Islands, British Columbia. North American Fauna 21:1-50.

Polderboer, E.B., L.W. Kuhn, and G.O. Hendrickson. 1941. Winter and spring habits of weasels in central Iowa. Journal of Wildlife Management 5:115-119.

Poole, K.G., and R.P. Graf. 1996. Winter diet of marten during a snowshoe hare decline. Canadian Journal of Zoology 74:456-466

Powell, R.A. 1994. Structure and spacing of Martes populations. Pp.101-121 In Martens, Sables and Fishers: Biology and Conservation. Buskirk, S.W., A.S. Harestad, M.G. Raphael, and R.A. Powell, eds. Cornell University Press. 484 pp.

Powell, R.A. 1982. Evolution of black-tipped tails in weasels: predator confusion. American Naturalist 119:126-131.

Powell, R.A. 1973. A model for raptor predation on weasels. Journal of Mammalogy 54(1):259-263.

Preble, E.A. 1898. Description of a new weasel from the Queen Charlotte Islands, British Columbia. Proceedings of The Biological Society of Washington 12:169-170.

Province of British Columbia. 1999. Managing Identified Wildlife: Procedures and Measures. Vol. 1. Ministries of Forests and Environment, Lands and Parks. Victoria, B.C. 180 pp.

Reid, Donald G., Louise Waterhouse, Peter E. F. Buck, Andrew E. Derocher, Rolf Bettner and Colin D. French. 2000. Inventory of the Queen Charlotte Islands Ermine. Pp. 393 - 406 In Proceedings of a Conference on the Biology and Management of Species and Habitats at Risk, Kamloops, B.C., 15 - 19 Feb., 1999, Laura M. Darling ed.. Volume One. B.C. Ministry of Environment, Lands and Parks, Victoria, B.C. and University College of the Cariboo, Kamloops, B.C. 490 pp.

Rosenzweig, M.L.. 1966. Community structure in sympatric Carnivora. Journal of Mammalogy 47:602-612.

Samson, C. and M. Raymond. 1998. Movement and habitat preference of radio tracked stoats, Mustela erminea, during summer in southern Quebec.

Sandell, M. 1986. Movement patterns of male stoats Mustela erminea during the mating season: differences in relation to social status. Oikos 47:63-70.

Simms, D.A. 1979a. North American weasels: resource utilization and distribution. Canadian Journal of Zoology 57:504-520.

Simms, D.A. 1979b. Studies of an ermine population in southern Ontario. Canadian Journal of Zoology 57:824-832.

Sullivan, T.P., and D.S. Sullivan. 1980. The use of weasels for control of mouse and vole populations in a coastal coniferous forest. Oecologia 47:125-129. (Referenced in Lisgo, 1999).

Thomson, I.D. and P.W. Colgan. 1990. Prey choice by marten during a decline in prey abundance. Oecologia 83:443-451.

Weckworth, R.P. and V.D. Hawley. 1962. Marten food habits and population fluctuations in Montana. Journal of Wildlife Management 26:55-73.

Weir, R.D. 1995. Diet, spatial organization and habitat relationships of fishers in south central B.C. M.Sc. thesis, Simon Fraser University, Vancouver, B.C., Canada. 139 pp.

Youngman, P. 1984. Status report on the Queen Charlotte Islands ermine Mustela erminea haidarum. Committee on the Status of Endangered Wildlife in Canada, Ottawa. 9 pp.

Zielinski W. J., W.D. Spencer, and R.H. Barrett. 1983. Relationship between food habits and activity patterns of pine martens. Journal of Mammalogy 64:387-396.

A. Edie is an independent consulting biologist, with a Master of Science Degree from the University of British Columbia. He is a former Regional Wildlife Biologist for the Skeena administrative region which includes Haida Gwaii. He has worked in the Skeena Region as a biologist or fish and wildlife administrator since 1978.

Alvin Breitkreutz – Former Conservation Officer, Queen Charlotte Islands (QCI); currently Regional Conservation Officer, Ministry of Environment, Lands, and Parks, Kamloops, B.C.

Dr. Melissa Fleming – Genetics researcher, Fred Hutchinson Cancer Research Center, Seattle, Washington, U.S.A.

Dr. Dave Hatler – Former regional biologist, Ministry of Environment, Smithers; currently an independent consultant in Enderby, B.C.

Mr. Herb Hughan – Former trapper near the Yakoun River in Haida Gwaii; currently a resident and trapper in the Nass Valley north of Terrace, B.C.

Mr. John Merriman – Former Conservation Officer in Haida Gwaii; currently an instructor at Malaspina College in Nanaimo, B.C.

Mr. David Nagorsen – Curator, Royal B. C. Museum, Victoria, B.C.

Dr. Donald Reid – Biologist, Ministry of Environment, Lands, and Parks, Smithers, B.C.

Mr. George Schultze – Wildlife technician, Ministry of Environment Lands and Parks, Smithers, B.C.

Collections were not consulted during preparation of this report. Descriptions of known specimens of the QCI ermine are summarized in Appendix 1.

Known Museum Specimens of QCI ErmineFootnote a.1
Cat_No Mus. Location Collector Coll. No. Specimen Sex Age TL TV HF EAR WT Date Remarks
0000019353 AMNH Graham Island; Masset Newcombe, C.F. skin and skull September 1900 Brown pelage
0000037411 AMNH No Island Specified Brown, W.W. 40 skin and skull male 290 75 40 18 20 August 1914 Brown pelage
0000038840 AMNH No Island Specified W. W. Brown 2 skull (skull smashed) male? 6 August 1914 Skin destroyed by dermestids
0000038841 AMNH No Island Specified W. W. Brown 1 skull (skull smashed) male? 11 August 1914 Skin destroyed by dermestids
0000042256 AMNH Graham Island Munro, J.A. 37B skin and skull 4 March 1918 White winter pelage
31207 MVZ Graham Island; Masset Brooks, A. Skull 20 May 1920 No measurements or field number
31208 MVZ Graham Island; Masset Brooks, A. Skull 20 May 1920 No measurements or field number
31209 MVZ Graham Island; Masset Brooks, A. Skull 20 May 1920 No measurements or field number
31210 MVZ Graham Island; Masset Brooks, A. Skull 20 May 1920 No measurements or field number
0000003100 CMN Graham Island J. A. Munro 14-17 skin and skull male adult 14 January 1917 In white pelage
0000008582 RBCM Graham Island; Yakoun River Hughan, H. skin; skull; skeleton male 270 73 36 115.00 27 February 1974 #513 prep EC #992
0000008583 RBCM Graham Island; Yakoun River Hughan, H. skin skull skeleton female 240 61 33 73.00 27 February 1974 White pelage
0000009944 RBCM ? Hatler, D. Skull female? Winter 77/78 Prep ec#950
0000009945 RBCM ? Hatler, D. Skull female? Winter 77/78 Prep ec#951
0000009946 RBCM ? Hatler, D. Skull female? Winter 77/78 Prep ec#952
0000009947 RBCM ? Hatler, D. Skull female? Winter 77/78 Prep ec#953
0000010196 RBCM ? Foster, J. Bristol skin; skull female 250 60 35 0 64.00 Win 1979 Year 1979 or 1980
0000010197 RBCM ? Foster, J. Bristol Skin male 284 72 43 0 108.00 Win 1979 Year 1979 or 1980
0000017658 RBCM Moresby Island Foote, K. skin; skull; skeleton male ? 282 72 40 20 118.00 Registered trapline
0000017659 RBCM Moresby Island Foote, K. skin; skull; skeleton male ? 280 70 39 18 105.00 Registered trapline
0000004841 UBC Skidegate E.C. Stevens 1971 skin & skull male January 1945
0000008771 UBC Tlell I. Richardson skin & skull male juvenile 278 73 37 1 October 1963
0000008772 UBC Tlell skin & skull male 285 73 38 December 1963
0000009093 UCLA Graham Island; Masset Brooks, A. skin and skull male 20 Aug 1920
0000094430 USNM Graham Island; Masset J. H. Keen skin and skeleton male adult 275 60 37 17 March 1898 Holotype
100622 USNM Moresby Island; Cumshewa Inlet W.H. Osgood 1053 skin, skull male June 21, 1900
100623 USNM Moresby Island; Cumshewa Inlet W.H. Osgood 1065 skin, skull female June 29, 1900
100624 USNM Moresby Island; Cumshewa Inlet W.H. Osgood 1066 skin, skull female June 29, 1900
100625 USNM Graham Island; Skidegate W.H. Osgood 1193 skin, skull male July 17, 1900
230777 USNM Graham Island; Mc Clinton Bay J.A. Munro 33 B skin, skull male March 25, 1918
15300 UWBM Graham Island J. A. Munro skin/ skull m 292 22 Feb 1918
American Museum of Natural History, New York
Museum of Vertebrate Zoology, Berkley
Canadian Museum of Nature, Ottawa
Cowan Vertebrate Museum, UBC, Vancouver
U.S. National Museum, Washington
U. of Washington Burke Museum, Seattle

As Mr. Herb Hughan has probably caught more QCI ermine than any other known trapper (Hatler, pers. comm), and as he was apparently not included among trappers reported in Reid et. al. (2000), A. Edie interviewed him in his home in the Nass Valley on October 29, 1999. The following is a summary of the results of that interview.

Mr. Hughan first trapped trapline 613T009 in roughly 1964, and purchased the line one year thereafter. (Dates here were intended by Mr. Hughan to convey the sequence of events more than the actual years on which events occurred. He was working from recollection only, and had no detailed memory of the specific years involved) This trapline was formerly owned by a Mr. Mike McNeil, and is located just north of Yakoun Lake on Graham Island.

Mr. Hughan had no written records of his ermine catch, and trapper return data do not exist for the time period being discussed (G. Schultze, pers. comm). Mr. Hughan’s recollection of ermine caught is as follows:

1964-1965
no ermine caught, but sign seen “once in a while”.
1966
2 ermine caught whole and provided to the then Fish and Wildlife Branch, 2 more caught but scavenged by marten.
1967
no ermine caught whole, probably 2 caught but scavenged.
1968
13 ermine caught whole and provided to Fish and Wildlife Branch, roughly equal number caught but scavenged.
1969
2 ermine caught whole and given to Haida Gwaii museum for mounting; probably 2 more caught but scavenged. The 2 specimens given to Haida Gwaii museum were apparently sent to the provincial museum for mounting, but were appropriated for collections and remained in Victoria. These are presumably the two specimens attributed to H. Hughan in Appendix 1. Dates for these specimens suggest that they may have been trapped a few years later than recalled by Mr. Hughan.
1970
2 ermine caught whole and given to Haida Gwaii museum, probably 2 more caught but scavenged.

All ermine were caught in old growth forest from 0 to 100 meters from the Yakoun River, none of them before Christmas. Salmon carrion was not available during the season that Mr. Hughan trapped. Most or all were caught with beaver meat as bait, supplemented by Mr. Hughan’s own scent lure composed of beaver castor, rancid fish oil, and skunk scent.

When asked why he thought he caught more ermine than other trappers, he responded:

  1. few trappers actively sought marten then,
  2. he used size 1 ½ traps exclusively for marten, which tended to kill weasels instantly by clamping them around the body, whereas the smaller traps used by most other trappers for marten would catch ermine by a leg which the ermine would chew off, and
  3. he used pole sets exclusively, which often resulted in trapped ermine hanging out of reach of scavenging marten, whereas other trappers he was familiar with used ground sets which in his opinion would result in virtually all ermine caught being scavenged by marten.

When asked why he thought so many weasels were caught in 1968, he said did not know why. A. Edie then asked whether he could recall noticing anything unusual about marten populations that might be related to the unusually high ermine catch. After thinking about the question, he recalled that during one year roughly around that time, marten in his area became very badly infested with the worst outbreak of ticks he has seen. He recalled discussing the matter with the local conservation officer who advised him that he could expect to catch a lot fewer marten next winter as a result of the ticks. His marten catch dropped to less than 30 the winter after the infestation, whereas in previous winters it was between 60 and 100. He had no specific recollection that the tick infestation occurred immediately before the exceptional ermine catch but suggested that trapping records should be able to confirm this because his marten catch definitely dropped dramatically after the infestation. Unfortunately, however, it was later determined that trapping records do not go that far back.

Mr. Hughan provided the following additional observations of ermine or ermine sign:

Mr. Hughan also provided the following general observations:

Ermine records existing prior to work by Reid et. al. (2000)Footnote a.2
Year Month Data source Record type Island Location
1898 Mar CDC TRD Graham Masset
1900 Jun RBM TRD Moresby Cumshewa Inlet
1900 Jun RBM TRD Moresby Cumshewa Inlet
1900 Jun RBM TRD Moresby Cumshewa Inlet
1900 Jul RBM TRD Graham Skidegate
1910 Aug RBM TRD ? ?
1910 Aug RBM TRD ? ?
1914 Mar RBM TRD Graham McClinton Bay
1914 Mar RBM TRD Graham ?
1916 May RBM TRD Graham Masset
1916 May RBM TRD Graham Masset
1916 May RBM TRD Graham Masset
1916 May RBM TRD Graham Masset
1916 Aug RBM TRD Graham Masset
1940 Dec RBM TRD Graham Skidegate
1945 Jan CDC TRD Moresby Skidegate Channel
1959 Nov RBM TRD Graham Tlell
1963 Dec CDC TRD Graham Tlell
1965 Aug RBM VO Moresby Takakia Lake
1973 Nov RBM TRD Graham Tlell
1974 Feb CDC TRD Graham Yakoun River
1974 Feb CDC TRD Graham Yakoun River
1974 Jan RB< TRD Graham Tlell
1975 Nov RBM TRD Graham Kumdis Creek
1975 Dec RBM TRD Graham Kumdis Creek
1986 Jan RBM TRD Moresby Selwyn Point
1986 Feb RBM VO Graham Juskatla Inlet
1987 Sep RBM VO Moresby Sachs Creek
1987 Jan RBM TRD Moresby ?
1987 Jan RBM TRD Moresby ?

CDC = Conservation Data Centre of the British Columbia Ministry of Environment

RBM = Royal British Columbia Museum

TRD = Trapped Dead

VO = Visual Observation

New records of QCI ermine collected by Reid et. al. (2000)Footnote a.3
Year Month Record typeFootnote b Location (Island/Drainage) Elev (m) Habitat typeFootnote c Forestharvest historyFootnote d Water typeFootnote e Dist. to water (m)
1900 ? VO Graham / Hancock 0 Beach UC MR / ES 5
1920 Fall VO Graham / Sewall 1 Bldg RC MR 55
1921 Spring OSI Graham / Sewall 1 Bldg RC MR 55
1922 April OSI Graham / Chinukundl 3 Bldg OC MR 35
1922 Summ. VO Graham / Sewall 1 Bldg RC MR 55
1922 Spring VO Graham / Sewall 1 Bldg RC MR 55
1924 Fall VO Graham / Sewall 1 Bldg ? MR 55
1926 Summ. VO Graham / Sewall 1 Bldg ? MR 55
1928 Dec VO Graham / Watun 0 PA OC MR 30
1928 Dec TRD Graham / Cape Ball ? ? ? ? ?
1928 Dec TRD Graham / Cape Ball ? ? ? ? ?
1928 Dec TRD Graham / Cape Ball ? ? ? ? ?
1928 Dec TRD Graham / Cape Ball ? ? ? ? ?
1928 Dec TRD Graham / Cape Ball ? ? ? ? ?
1928 Dec TRD Graham / Cape Ball ? ? ? ? ?
1928 Jul VO Graham / Masset 0 FE UC MR 50
1930 Jan TRD Graham / Yakoun ? CF UC RI 25
1930 Jan TRD Graham / Yakoun ? CF UC RI 25
1935 Jan VO Graham / Skidegate 2 PA OC CR 5
1936 Mar VO Graham / Cape Ball 60 FE UC RI 150
1936 Mar VO Repeat
1936 Feb TRD Graham / Yakoun ? CF UC CR 15
1936 Feb TRD Graham / Yakoun ? CF UC CR 15
1936 Feb OSI Graham / Yakoun ? CF UC CR 15
1939 Jun VO Moresby / Cumshewa 0 CF OC MR ?
1940 Nov VO Graham / Ain 0 CF UC MR / ES 50
1940 Sep VO Graham / Tlell ? Bldg UC RI 8
1943 Jan TRD Graham / Kumdis 0 CF UC MR 50
1944 Jan TRD Graham / Kumdis 0 CF UC MR 50
1945 Jul VO Graham / Fife Pt 5 Bldg UC MR 150
1945 Feb VO Graham / Tlell ? Bldg UC MA 25
1946 Dec VO Graham / Danube 30 Bldg UC LA 300
1946 Nov OSI Graham / Fife Pt ? Bldg UC ES ?
1947 Jan VO Moresby / Skidegate 10 PA OC CR 20
1947 Jan VO Repeat
1947 Jul OSI Graham / Fife Pt 5 Bldg UC MR 150
1952 Jul VO Moresby / Copper 5 CF OC MR 6
1963 Sep VO Graham / Cape Ball 3 PA UC ES / RI 10
1964 Mar CAT Graham / Tlell ? ? ? ? ?
1965 Fall VO Graham / Mayer ? MF UC CR 500
1967 Feb TRD Graham / Masset 0 CF UC MR 3
1967 Feb TRD Graham / Masset 0 CF UC MR 3
1968 Fall VO Graham / Mayer 15 CF UC CR ?
1972 Aug VO Graham / Tarundl 0 Beach OC MR 3
1972 Jul VO Graham / Honna 0 FE OC MR 3
1972 Wint. VO Graham / Mayer ? BO UC MA 30
1972 Wint. VO Graham / Mayer ? BO UC MA 30
1972 Wint. VO Graham / Mayer ? BO UC MA 30
1972 Wint. VO Graham / Mayer ? BO UC MA 30
1973 Wint. VO Graham / Marie ? CF UC LA 40
1973 Wint. VO Graham / Marie ? CF UC LA 40
1973 Wint. VO Graham / Marie ? CF UC LA 40
1973 Wint. VO Graham / Marie ? CF UC LA 40
1973 Wint. VO Graham / Marie ? CF UC LA 40
1973 Wint. VO Graham / Marie ? CF UC LA 40
1973 Wint. VO Graham / Marie ? CF UC LA 40
1974 Apr VO Moresby / Lagoon 10 CF RC MR 20
1974 Apr VO Moresby / Lagoon 0 Beach UC MR 5
1975 Nov VO Graham / Yakoun 20 CF OC RI 100
1975 Jan VO Graham / Blackwater ? CF OC CR 60
1975 Jan STR Graham / Coho ? CF UC CR 10
1975 Wint. TRD Graham / Mayer 15 FE UC RI 10
1975 Wint. TRD Graham / Mayer 15 FE UC RI 10
1978 Dec VO Graham / Yakoun ? CF OC RI 800
1978 Aug VO Graham / Tlell 20 BO UC CR 50
1978 Spring VO Graham / Mayer 15 CF UC CR ?
1979 May VO Graham / Yakoun 10 CF UC RI 130
1980 Nov VO Graham / Slatechuck 0 ME OC MR 10
1980 Sep VO Moresby / Skaat 0 Beach UC MR 0
1980 Apr OSI Graham / Lawnhill 15 Bldg OC CR 80
1980 Jan VO Graham / Masset 30 CF UC MR 400
1981 Jan TRD Moresby / Alliford Bay 500 CF OC MR 350
1981 Jan VO Graham / Chinukundl 3 CF OC MR 30
1981 Nov VO Graham / Blackwater ? CF RC CR 10
1982 Dec TRD Graham / Chown 0 CF UC RI 10
1982 Jan TRD Graham / Deep 0 MF UC CR 10
1982 Jan TRD Moresby / Alliford Bay ? CF OC CR ?
1983 Dec VO Louise / Beatty Anch. 10 Bldg OC MR 50
1983 Oct VO Graham / Yakoun ? CF OC RI 35
1983 Wint. VO Graham / Port Clements 1 Bldg OC CR 11
1984 Nov VO Graham / Yakoun ? CF OC RI 7
1984 Nov VO Graham / Mayer ? BO UC MA 35
1985 ? VO Moresby / South Bay Rd ? CF OC MR 500
1985 Nov VO Graham / Datlamen 20 CF RC RI 300
1985 Jan TRD Burnaby/ Dolomite ? CF UC MR 500
1986 ? VO Graham / Yakoun ? CF UC CR ?
1986 Jul Vo Moresby / South Bay Rd 75 CF RC MA 350
1986 Jul VO Louise / Mathers 1500 CF RC MR 1600
1986 Jul VO Repeat
1986 Jan VO Graham / Miller 5 MF ? MR 30
1986 Jan TRD Moresby / Mosquito ? CF OC LA 300
1986 Feb VO Graham / Mayer ? BO UC MA 30
1986 Feb VO Graham / Mayer ? BO UC MA 30
1987 Dec VO Graham / Yakoun ? CF OC RI 5
1987 Nov VO Graham / Yakoun 10 CF UC RI 75
1987 Sep VO Graham / Brent 250 CF OC CR 1
1987 Jun VO Graham / Brent 0 Bldg UC MR 15
1987 Feb VO Graham / Phantom ? CF UC CR 75
1988 Jul VO Graham / Rose Spit 0 Beach UC MR 70
1988 Jul VO Repeat
1989 Dec VO Graham / Florence ? CF RC ? 1000
1989 Sep VO Graham / Tlell ? CF UC MA 20
1989 Jul VO Graham / Gold ? CF RC RI 4
1989 Feb VO Graham / Kumdis 15 CF OC CR 100
1991 ? VO Graham / Kagan 800 CF UC LA 50
1991 Nov VO Moresby / Sandspit 1 Beach OC MR 30
1991 Jul VO Graham / Mayer ? CF UC ? ?
1991 Jul CAT Graham / Tlell ? ? ? ? ?
1991 Jun VO Graham / Watun 0 CF UC ES / RI 5
1991 Feb STR Moresby / Mosquito 10 CF OC LA 80
1991 Jan TRD Moresby / Mosquito ? CF OC MR / CR ?
1991 Sep VO Graham / Tian Head 0 CF UC MR 5
1992 Dec VO Graham / Yakoun ? CF OC RI 200
1992 Dec STR Moresby / Chroustcheff 5 PA OC MR ?
1992 Jul VO Graham / Phantom ? CF RC RI 1000
1992 Jul VO Graham / Yakoun ? CF RC ? ?
1992 Mar VO Moresby / Copper ? MF OC MR 21
1992 Feb VO Graham / Miller 50 MF UC CR 60
1992 Jan STR Graham / Sue ? CF RC / OC CR ?
1993 Dec VO Graham / Yakoun ? SH RC RI 50
1993 Oct VO Graham / Mamin ? CF RC CR 200
1993 Sep VO Louise / Skedans 1 CF OC MR 5
1993 Jul VO Moresby / Copper 1 Beach OC MR 10
1993 Jun VO Graham / Tlell 3 DF OC MR 25
1993 Apr VO Graham / Lawn Pt 1 MF OC MR 40
1993 Feb VO Graham / Yakoun ? CF OC RI 200
1993 Jan VO Graham / Gregory 5 CF OC RI 200
1993 Nov VO Graham / Mayer ? CF UC MA 30
1994 Dec VO Moresby / Sachs 15 CF OC MR /CR 200
1994 Jul VO Graham / Riley ? CF UC ? ?
1994 Mar VO Graham / QC City 8 CF OC MR 500
1994 Feb STR Graham / Survey ? CF RC CR 100
1994 Jan VO Graham / Yakoun ? CF UC CR 100
1995 Oct VO Graham / Towhill 10 MF OC RI 200
1995 Sep VO Graham / Yakoun ? CF UC RI 20
1995 Jul VO Graham / Rennell 5 CF OC MR 25
1995 Mar VO Graham / Mamin 400 CF UC / RC CR 50
1995 Jan STR Graham / Survey ? CF OC CR 80
1996 Dec STR Moresby / Deena 1 CF OC MR 10
1996 Dec VO Graham / Kumdis 50 MF UC CR 300
1996 Oct VO Graham / Davidson ? CF RC CR 12
1996 Sep VO Graham / Delkatla 0 CF OC ES 10
1996 Sep VO Repeat
1996 Jul VO Graham / Yakoun 250 CF OC RI 50
1996 Mar VO Graham / Yakoun ? CF OC CR / RI 20
1996 Feb TRD Graham / Honna ? ? ? ? ?
1996 Feb VO Graham / Yakoun ? CF OC CR 10
1996 Feb VO Graham / Yakoun ? CF OC CR 10
1996 Jan VO Graham / Mayer 50 BO UC MA 15
1997 Aug VO Graham / Masset 10 MF OC CR 250
1997 Aug VO Moresby / Sachs 1 CF OC MR / CR 0
1997 Aug VO Graham / Kumdis 50 CF UC / RC MA 100
1997 Aug VO Moresby / Blaine 10 CF OC MR 240
1997 Aug VO Moresby / Heather 20 CF RC CR ?
1997 Jul VO Graham / Lawnhill 3 MF UC MR 30
1997 Jun VO Moresby / Government ? CF UC RI 0
1997 May VO Graham / Towhill Rd 0 MF OC MA 60
1997 Feb TRD Graham / Honna 200 CF OC LA 500
1997 Aug CAT Graham / QC City ? ? ? ? 600
1997 July VO Graham / Lawnhill 10 CF UC CR ?
1997 Nov VO Graham / Mamin 30 CF RC RI 200
1997 Nov VO Graham / Mamin 20 CF OC RI 500

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