Printer Friendly

Long-term control of Peary caribou numbers by unpredictable, exceptionally severe snow or ice conditions in a non-equilibrium grazing system.

ABSTRACT. The number of Peary caribou (Rangifer tarandus pearyi) on the Queen Elizabeth Islands, Canadian High Arctic, is at an all-time known low. Yet some populations are still hunted, and there is no adequate monitoring program in place to determine the consequences. We evaluate information from the Peary caribou population on the south-central Queen Elizabeth Islands as a standard for an accurate and realistic assessment of what controls Peary caribou population dynamics. Between 1973 and 1997, major population crashes related to severe winter or spring weather are known to have occurred on the south-central Queen Elizabeth Islands in four caribou-years (i.e., 1 July-30 June). Population losses were 67% in 1973-74, 33% in 1994-95, 78% in 1995-96, and 83% in 1996-97. There is no evidence for direct density-dependent responses during either the favorable weather years of population growth or during any one of the years with a disastrous die-off. It appears that Peary caribou on the Queen Elizabeth Islands are living in a non-equilibrium grazing system driven mainly by abiotic factors (emergent properties), particularly by exceptionally unfavorable snow or ice conditions. Changing levels of predation by the High Arctic gray wolf (Canis lupus arctos) compound the uncertainty. In this High Arctic ecosystem, non-equilibrium-governed population dynamics plus wolf predation represents an appropriate conceptual model for Peary caribou populations on the Canadian High Arctic islands. The application of our findings to decision making, together with an adequate monitoring program by the responsible agencies, would promote the biological management and ecological conservation of Peary caribou on the Queen Elizabeth Islands.

Key words: Arctic Canada, population dynamics, Rangifer tarandus pearyi, weather-related density-independent population crashes

RESUME. Le nombre de caribous de Peary (Rangifer tarandus pearyi) repertories dans les iles de la Reine-Elisabeth, Extreme-Arctique canadien, se trouve au niveau le plus bas a n'avoir jamais ete enregistre. Pourtant, certaines populations font toujours l'objet de la chasse et il n'existe aucun programme de surveillance adequat pour en determiner les consequences. Nous evaluons ici des donnees relatives a la population de caribous de Peary des iles centre-sud de la Reine-Elisabeth afin d'aboutir a une norme d'evaluation precise et realiste pour determiner ce qui influence la dynamique de population des caribous de Peary. Entre 1973 et 1997, d'importants declins de population attribuables aux hivers ou aux printemps rigoureux ont ete enregistres dans le centre-sud des iles de la Reine-Elisabeth sur une periode de quatre annees-caribous (c'est-a-dire du [] juillet au 30 juin), Les declins de population se sont eleves a 67 % en 1973-1974, 33 % en 1994-1995, 78 % en 1995-1996 et 83 % en 1996-1997. Il n'existe aucune preuve de resultats directs dependant de la densite pendant les annees de croissance de la population au cours desquelles les conditions meteorologiques etaient favorables ou pendant l'une ou l'autre des annees de desastreux declins. Il semble que le caribou de Peary des iles de la Reine-Elisabeth vive dans un systeme de paturage hors equilibre repondant principalement a des facteurs abiotiques (proprietes emergentes), surtout lorsque les conditions d'enneigement ou de glaciation sont exceptionnellenient defavorables. L'incertitude est aggravee par les taux de predation changeants chez le loup arctique (Canis lupus arctos). Dans cet ecosysteme de l'Extreme-Arctique, les dynamiques de population hors equilibre, alliees a la predation par le loup, representent un modele conceptuel adequat pour les populations de caribous de Peary des iles de l'Extreme-Arctique canadien. La gestion biologique et la conservation ecologique du caribou de Peary dans les iles de la Reine-Elisabeth auraient avantage a tenir compte des constatations emanant de notre etude dans la prise de decisions de meme que d'un programme de surveillance convenable de la part des organismes responsables.

Mots cles: Arctique canadien, dynamique de population, Rangifer tarandus pearyi, declins de population independants de la densite attribuables aux conditions meteorologiques

Traduit pour la revue Arctic par Nicole Giguere.


Aboriginal peoples of northern Canada view the use of caribou (Rangifer tarandus) as central to their cultures; therefore, the conservation of those caribou is complicated. Most of those caribou populations are subjected to year-round hunting by aboriginal people, either without kill limits or, if regulations exist, without enforcement of those limits. It is not practical in this situation to attempt to conserve these caribou populations at small sizes, as the preservation of unharvest-able caribou populations will not be seen by the aboriginal users as a satisfactory long-term solution. Thus, an accurate and realistic assessment of what controls Peary caribou (R. t. pearyi) population dynamics must be a first step in both their biologically sound management for human consumption and their ecologically sound conservation for preservation.


Peary caribou on the Queen Elizabeth Islands (QEI: Fig. 1) live at the edge of the species' range (Miller and Gunn, 2003b) and, perhaps more importantly, on range that approaches the limits of plant growth (Edlund and Alt, 1989; Edlund, 1990) and experiences extreme weather perturbations (Maxwell, 1981). Such peripheral populations are usually more susceptible to density-independent limiting factors (Crete et al, 1996), and we suggest this is the case for these Peary caribou. The number of Peary caribou on the QEI is now at an all-time known low (Miller and Gunn, 2003b). The overall decline of population numbers on the QEI accelerated and deepened as a result of several major to cataclysmic weather-related die-offs (crashes) between 1973 and 1997. In all four of the die-off years, the crashes occurred in association with prolonged and exceptionally severe snow or ice conditions in winter or spring (Parker et al., 1975; Miller et al., 1977a; Miller, 1998; Gunn and Dragon, 2002; Miller and Gunn, 2003a, b).

Those remaining Peary caribou now potentially face additional future uncertainties from climate change and pervasive negative changes in their environment (Maxwell, 1997; Weller, 2000; Comiso, 2002; Miller and Gunn, 2003b; Miller et al., 2005b). If those changes proceed as predicted, Peary caribou might not be able to cope with the new conditions and still reach population sizes that will support desired levels of annual harvest by aboriginal hunters (Gunn et al., 2000, 2003; Miller and Gunn, 2003b). For these reasons, and because the data support the primary importance of weather in the prosperity--and at times, the very persistence--of Peary caribou populations, our objective here is to detail what really controls Peary caribou population dynamics on the QEI. We focus on the Peary caribou population found on the south-central QEI, which has the best documentation, as a case study. We believe the findings will be applicable to most, if not all, Peary caribou on the QEI.



Peary caribou and muskoxen (Ovibos moschatus) are the only two ungulates that have established themselves on the QEI. The High Arctic gray wolf (Canis lupus arctos) is also found throughout the QEI in association with its major prey base--Peary caribou and muskoxen (Miller, 1995c; Miller and Reintjes, 1995). Miller et al. (2005a) identified five eco-units in the QEI: southwest (SW), south-central (S-C), northwest (NW), north-central (N-C), and eastern (E). Of these, the SW and S-C eco-units have served as the "heartland" for Peary caribou, at least during the last half of the 20th century (Fig. 1). Peary caribou were abundant in the NW eco-unit in 1961, but rare and probably absent at times thereafter. Caribou have been uncommon to rare from at least 1961 onward in the N-C and E eco-units.

Data Sources

We used data from Tener (1963), Slaney (1975), Fischer and Duncan (1976), Miller et al. (1977a), Ferguson (1987), Miller (1987, 1989, 1991, 1992, 1993, 1994, 1995b, 1997, 1998), Gunn and Dragon (2002), and Miller and Gunn (2003a) to determine the size, trend, and reproductive performance of the five-island Peary caribou population on the south-central QEI between 1961 and 1998 (Figs. 1, 2). We adjusted Tener's (1963) 1961 caribou estimate of 3565 for the five-island complex to 3509 to correct for differences in island sizes used by Tener (1963) and those currently reported in The Atlas of Canada (, under Facts about Canada, Sea Islands).

Because published estimates for 1993 and 1994 were based on slightly different land areas (Miller, 1998:35) and to maintain a constant survey area among all years, we made the following changes. To obtain a 1993 estimate, we conservatively expanded the 2387 caribou counted in the 1993 non-systematic aerial survey by taking the number of caribou counted on Bathurst, Alexander, and Massey islands in 1993 and multiplying it by the average annual growth rate from 1985 to 1988 (i.e., the last two surveys prior to 1993). Since fog had prevented a survey on Ile Vanier and Cameron Island in 1993, we added to the estimate 106 animals, extrapolated from the average of 1985 and 1988 values for those two islands (Table 1: i.e., (2387 x 1.123) + 106 = 2787). We then conservatively obtained a 1994 estimate by multiplying our 1993 estimate by the average annual growth rate between 1974 and 1993 (Table 1: i.e., 2787 x 1.132 = 3155) as a reasonable expansion from 1993. These calculations resulted in a 120-animal (4%) increase (from 2667 to 2787) in the 1993 estimate and a 144-animal (5%) increase (from 3011 to 3155) in the 1994 estimate over previously reported values.


As a measure of calving success, we used the percentage of calves observed among all caribou seen during a single post-calving count made between the end of June and late August each year to determine sex and age composition. We based this measure on the assumptions that most calf mortality occurs at birth or within the first week of life (Miller et al., 1988) and that maximum representation of newborn calves would be 30% among all caribou seen (i.e., [r.sub.m] - 0.30; Bergerud, 1980), assuming minimal mortality around calving time among animals one year old or older. We also evaluated the performance of breeding cows using two ratios obtained from each annual count: the number of calves per 100 breeding cows and the number of calves per 100 females age one year or older (l+-year-old females).

W.A. Gould (pers. comm. 2008) provided us with the tabulated data (derived from GIS polygons of vegetation classes) that were used to produce the vegetation maps in Gould et al. (2003: Figs. 3, 4, and 5). We grouped those data for our five-island study area into two vegetation types, "High Arctic semidesert" and "polar desert." We then obtained estimates of the area represented by each vegetation type by island and adjusted them to conform to the sizes reported in The Atlas of Canada for Bathurst, Vanier, Cameron, Alexander, and Massey islands (http://atlas., under Facts about Canada, Sea Islands). Then we estimated the oven-dried weight for the total annual aboveground net primary production (kg * [km.sup.-2] * [y.sup.-1]) of each vegetation type by island, using those rates from Bliss and Matveyeva (1992: Table III). High Arctic semidesert vegetation was calculated at 25 000 kg * [km.sup.-2] and polar desert vegetation at 700 kg * [km.sup.2] times their respective area of coverage ([km.sup.2]) on each island.

Working Definitions

We use the term "crash" to identify all major die-offs that occur within a population in a single caribou-year (1 July-30 June; Miller and Gunn, 2003b:215-216) that meet the criteria of Miller et al. (2005c:188). That is, a population crash must be (a) unpredictable, (b) rapid within a single caribou-year, and (c) result in a population decline of 30% or more in that year. Crashes occurring in consecutive years should be considered multiples of single-year events. For example, the consecutive three-year disastrous 98% decline in the Peary caribou population on the south-central QEI resulted from three annual crashes: 1994-95, 33% decline; 1995-96, 78%; and 1996-97, 83%.

We define the negative aspect of a "density-dependent factor" as one that affects the ability of a caribou population to continue to grow as a direct result of that population's density. A density-dependent factor would retard population growth, as the density increases beyond a hypothetical equilibrium point (K) by decreasing births and increasing deaths.

We define a "density-independent factor," such as exceptionally unfavorable snow or ice conditions, as one that negatively influences a caribou population, but that is independent of the existing population's density and its absolute forage supply. Thus, a density-independent factor (i.e., the chance occurrence of abiotic weather factors) is free of any fixed hypothetical equilibrium point.

We define "High Arctic semidesert" as those sections of the five-island study area having a 5-50% vegetation cover, based on a horizontal structure canopy; 100-500 g * [m.sup.-2] aboveground plant biomass; and 20-50 g * [m.sup-2] * [y.sup.-1] annual above and belowground net primary productivity (from Gould et al., 2003: Figs. 3, 4, and 5).

We define "polar desert" as those sections of the five-island study area with less than 5% horizontal structure as vegetation cover; less than 100 g * [m.sup.-2] aboveground plant biomass; and 0-20 g * [m.sup.-2] * [y.sup.-1] annual above and belowground net primary productivity (from Gould et al, 2003: Figs. 3,4, and 5).
TABLE 1. Population dynamics exhibited by the Peary caribou (Rangifer
tarandus peari) on Bathurst, Vanier, Cameron, Alexander, and Massey
islands within a 19 143 km (2) survey area, south-central Queen
Elizabeth Islands, Candian High Arctic, 1961 97.

Survey      Total      Density           Mean Annual    Source
Year (1)    Caribou    (caribou * 100    Growth Rate
                       [km.sup.-2])      ([lambda])

1961         3509           18.3              -         Tener (1963)

1973          797            4.2            0.884       Miller etal.

1974 *        266 *          1.4 *          0.334 *     Miller etal.

1975          361            1.9            1.357       Fischer and
                                                        Duncan (1976)

1981 (2)      345            1.8            0.993       Ferguson (1987)

1985          727            3.8            1.205       Miller (1987)

1988         1030            5.4            1.123       Miller (1989)

1993 (3)     2787           14.6            1.220       Miller (1995b,

1994 (4)     3155           16.5            1.132       Miller (1997,

1995 *      2100 *          11.0 *          0.666 *     Miller (1997,

1996 *      452 *            2.4 *          0.215 *     Miller (1998)

1997 *      78 *             0.4 *          0.173 *     Gunn and Dragon

(1) Bold indicates with * weather-related crash years.

(2) Ferguson (1987) estimated 289 caribou on Bathurst Island only in
August 1981; we adjusted his estimate to 345 caribou for the total
five-island area, basing the calculation on the proportionate land
area of Bathurst Island.

(3) The 1993 estimate equals the number of caribou counted on Bathurst,
Alexander, and Massey islands times the mean annual growth rate
([lambda]) for 1985 to 1988, plus 106 animals extrapolated from the
average of 1985 and 1988 values for lie Vanier and Cameron Island, to
maintain the 19 143 km (2) survey area in all years, i.e.,
(2387 x 1.123) 106 = 2787.

(4) The 1994 estimate equals the 1993 estimate times the mean annual
growth rate ([lambda]) for 1974-93, i.e., 2787 x 1.132 = 3155.


Population History

As an example, we use the Peary caribou population for which we have the most available information. It is found on five islands--Bathurst (16042 [km.sup.2]), Vanier (1126 [km.sup.2], Cameron (1059 [km.sup.2], Alexander (484 [km.sup.2]) and Massey (432 [km.sup.2])--covering a total 19 143 [km.sup.2] of range within the south-central QEI (Table 1, Fig. 2). The highs and lows of the Peary caribou and muskox populations within the south-centra! QEI paralleled each other through at least 1973-97 (Fig. 3).


The first systematic aerial survey of Peary caribou and muskoxen on the QEI to cover nearly their entire range was carried out in summer 1961 (Tener, 1963). That survey has served as the benchmark for determining trends in numbers and distribution of Peary caribou (and muskoxen) on the QEI (Miller et al., 2005a). Little information about the numbers and distributions of Peary caribou and muskoxen on the QEI was available before 1961. Local knowledge was limited, as only two small and isolated Inuit settlements existed on the QEI, having just been established there in the mid 1950s. These were Resolute Bay (74.72[degrees] N, 94.98[degrees] W) on the southwestern coast of Cornwallis Island and Grise Fiord (76.42[degrees] N, 82.91[degrees] W) on the south coast of Ellesmere Island).

In 1961, the Peary caribou population size was at an all-time known high (Table 1). Unfortunately, no one will ever know whether the population was at a peak, still coming up, or already going down. Nor are there any data on the pattern or causes of the decline that occurred during the next 12-year period (1961 -62 to 1972-73), when the population fell by 77%. Then, in 1973-74, the population crashed a further 67% in just one year (Fig. 3). Recovery was slow. The caribou population increased by ca. 4%*[y.sup.-1], on average, over the first seven years after the crash (1974-75 to 1980-81). Over the next 13 years (1981-82 to 1993-94), the population increased to 9.1 times its estimated 1981 size. The 20-year growth phase then ended abruptly. In three years (1994-95 to 1996-97), three single-year winter or spring weather-related crashes reduced the population to only a remnant, ca. 2-3% of its 1961 or 1994 size (Table 1, Fig. 3: Miller et al., 1977a; Miller, 1998; Gunn and Dragon, 2002).
TABLE 2. Area representation and annual aboveground net primary
productivity, by island of the two major vegetation types on the
five-island study area, south-central Queen Elizabeth Islands.
Vegetation Type by Island (Island Size)

                        Vegetation Type by Island (Island Size)
Vegetation Type (1)  Bathurst (16042  Vanier (1126  Cameron (1059
                     [km.sup.2])      [km.sup.2)    [km.sup.2])

Area ([km.sup.2]) representation of vegetation type by island (2)

High Arctic                 10995           1126           714

Polar desert                 5047              0           345

Annual aboveground net primary productivity (kg * [km.sup.-2] *
[y.sup.-1]) of each vegetation type by island (3)

High Arctic             274875000       28150000      17850000

Polar desert              3532900              0        241500

                  Vegetation Type by Island (Island Size)

Vegetation    Alexander (484 [km.sup.2]  Massey (432 [km.sup.2])
Type (1)

Area ([km.sup.2]) representation of vegetation type by island (2)

High Arctic                484                        432

Polar desert                 0                          0

Annual aboveground net primary productivity (kg * [km.sup.-2] *
[y.sup.-1]) of each vegetation type by island (3)

High Arctic           12100000                   10800000

Polar desert                 0                          0

1 See MATERIALS AND METHODS for working definitions of High Arctic
semidesert and polar desert, based on Figures 3, 4, and 5 of Gould
et al. (2003).

2 Obtained from tabular data used to produce Figures 3,4, and 5 of
Gould et al. (2003), which W.A. Gould (Dec 2008) provided directly
to us. We adjusted the five island sizes slightly to conform exactly
with those island sizes reported in The Atlas of Canada (http://atlas, under Facts about Canada, Sea Islands).

3 Total annual dry weight values for aboveground net primary
productivity ([kg * [km.sup.-2][y.sup.1]) of vegetation were calculated
by island from Bliss and Matveyeva (1992), at 25 000 kg * [km.sup.-2]
for High Arctic semidesert and 700 kg * [km.sup.-2] for polar desert,
then multiplied by the respective area ([km.sup.-2]) of representation
on each island.

Satellite and conventional VHF radio telemetry studies of Peary caribou on the south-central QEI indicate that various patterns of seasonal range occupancy are carried out annually (Miller, 1995a, 1997, 1998, 2002; Miller and Barry, 2003). Some caribou move annually on a seasonal basis among all five islands; others restrict their annual seasonal movements to only two, three, or four of those islands; and still others remain year-round on a single island. On Bathurst Island, some caribou remain year-round on the NE survey stratum, while others remain on the NW or S of the island (Fig. 2). Peary caribou on the south-central QEI seem to be exercising nearly every alternative pattern of seasonal and annual range occupancy available to them. The size of their seasonal range was smallest in winter and largest in summer, and their greatest displacements occurred during the pre-calving and pre-rut periods (Miller, 2002; Miller and Barry, 2003).

Forage Availability

The vegetation on the QEI has been described by Edlund and Alt (1989), Bliss (1990), Edlund (1990), and Gould et al. (2003), among others. Vegetation on the south-central QEI is limited compared to vegetation on the mainland tundra, but much of the caribou range is relatively productive for the QEI (Table 2; Gould et al., 2003: Figs. 3, 4, 5). About 72% of the 19 143 [km.sub.2] study area is High Arctic semidesert, and the remainder is polar desert (Table 2).

We estimate that on average, the 13 751 [km.sub.2] of High Arctic semidesert yields 25 000 kg * [km.sub.-2] of aboveground vegetation per year, whereas the 5392 [km.sub.2] of polar desert yields an average of only 700 kg * [km.sub.-2]. That is, annual production per [km.sub.2] of the High Arctic semidesert is 36 times that of the polar desert. The 72% of the study area in High Arctic semidesert could thus produce about 91 times as much aboveground new plant growth each year as the 28% of the study area in polar desert. Although 99% of the estimated new aboveground plant growth occurs annually on the High Arctic semidesert areas, the more exposed polar desert areas are most likely important to Peary caribou for short periods (several days or a few weeks) when accessibility of the forage supply has been temporarily and critically restricted nearly range-wide by extreme snow or ice conditions.

The total estimated annual production of aboveground vegetation in both High Arctic semidesert and polar desert is 347 549 400 kg (Table 2). The annual dry weight forage requirement of Peary caribou has been estimated at 730 kg * [caribou.sub.1] (Miller, 1998). Therefore, it appears that even the two largest numbers of Peary caribou ever estimated on the five-island study area, 3509 in 1961 and 3155 in 1994 (Table 1), would have required only about 1% of that total annual production for all to have survived. If the Peary caribou within the 19 143 [km.sub.2] study area could obtain even 2% of the estimated total aboveground vegetation production each year, those five islands could collectively support 10000 Peary caribou.

Thus, there is no evidence to suggest that wintertime forage accessibility in the study area was always inadequate to maintain the annual numbers of caribou that were estimated between 1961 and 1998. To the contrary, the annual rates of reproduction and early calf survival were high, and the study population was in an overall growth phase from 1974-75 though 1993-94 (Tables 3, 4, 5, Fig. 3). The level of population performance was high even compared to the levels of large, established mainland caribou populations. Also, in those 20 years, mortality among 1+-yr-old caribou was so low that it was nearly undetectable: we observed at most three carcasses per year, and none in some years, during 60-100 h of low-level helicopter search efforts in each year from 1988 to 1994, when the population was estimated to have increased 3.1 times (Table 1).

Population Dynamics

No data or empirical observations suggest that snow cover reduces Peary caribou access to forage to a small fraction of the total vegetated area in all years: it is only in those few years with exceptionally severe snow or ice conditions that such extreme restriction occurs. In fact, the snow cover is relatively shallow compared to mainland caribou winter ranges, and in many years, snowpack conditions (i.e., hardness, density, and icing on, in, or under the snowpack) are highly favorable throughout the period of snow cover, with icing alone in those years not being a problem (Miller, 1992, 1993, 1994). When the snow remains powdery with some granular ("sugar") snow on the bottom, the caribou can feed everywhere, except in some relatively small areas of deep depression or in snowdrift areas at the bases of steep slopes or cliffs. In years of favorable snow conditions, the caribou do not even have to crater--they simply push the snow cover aside with their noses (Miller, 1995b).

In some years, subtle environmental pressures can act on the caribou, with only relatively small reductions in population performance; in other years, the impact from unfavorable snow or ice conditions can lead to poor calf production and markedly reduced early calf survival, and in a few years, to near-total failure of the calf crop. Only a few unpredictable years with exceptionally extreme and prolonged snow or ice conditions are known to have caused single-year crashes (Figs. 3, 4).

Most importantly, no one has ever documented even small-scale local overgrazing, let alone an extensive area of severely deteriorated or destroyed range, caused by caribou grazing on the south-central QEI or anywhere else in the QEI. In the summer of 1998, which was the first summer after the three consecutive annual crashes that caused a 98% loss of the Peary caribou study population, Greg Henry, an experienced Arctic range ecologist, did a visual assessment, on foot and by low-level helicopter flights, of the vegetation on Bathurst Island. He concluded that the post-die-off range on Bathurst Island could support at least several thousand caribou without their having any serious impact on the vegetation (G.H.R. Henry, pers. comm. 1998).

Gunn and Dragon (2002) argue that it was not the caribou's absolute forage supply that caused the major crashes, for the following reasons:

1. During the weather-related crashes, population reductions occurred at high and similar mortalities among both Peary caribou and muskoxen--two species with important differences in diets and temporal and spatial selection of feeding sites--over a vast geographic region throughout the western QEI (ca. 100000 [km.sup.2]) (Miller et al., 1977a; Miller, 1998). (Fig. 3 shows the crashes for the south-central QEI only.)

2. The QEI have different regional climatic and vegetation patterns, constituting distinctive "bioclimatic zones" (Maxwell, 1981; Edlund and Alt, 1989; Edlund, 1990).

3. There is no evidence of changes in range occupation, or in daily, seasonal, or annual movement patterns, prior to the severe winters and springs. Such alterations would be expected in response to a seriously reduced forage supply that could no longer support the animals using it.

4. It appears that only extreme environmental episodes could cause deaths among Peary caribou and muskoxen that are correlated both spatially and temporally to such a degree.

The 20-year period (1974-75 to 1993-94) is the only period of continual population growth for a Peary caribou population on the QEI that is known and relatively well-documented (Table 1, Fig. 3). In the first 11 years (1974-75 to 1984-85), when densities were only 1.4 to 3.8 caribou* 100 [km.sup.-2], the mean annual growth rate ([lambda]) was 1.096. Over the next nine years (1985-86 to 1993-94), as caribou more than quadrupled, the densities increased from 3.8 to 16.5 caribou* 100 [km.sup.-2], and the mean annual growth rate ([lambda]) was 1.177, or 1.8 times that of the earlier period of low caribou densities. Mean calving success, measured as all calves among all caribou, was 25.3% [+ or -] 3.7% SD (range = 18.6-28.6%), where 30% calves would be the expected maximum. These high annual levels of reproduction and early calf survival could not have persisted throughout 1988-94 if the population's breeding cows had not been healthy, with high body fat reserves (Thomas, 1982). Thus, annual reproduction did not decrease with increasing population density, and the mean annual growth of the caribou population accelerated as density increased rather than decelerating, as in a density-dependent response (Table 1, Fig. 3). This pattern of better performance at higher densities offers no evidence for an inadequate absolute forage supply and the presence of population control by density-dependent factors.

After the 20-year growth phase, the 98% Peary caribou population decline and the 91% muskox population decline both followed immediately in 1994-95 to 1996-97. Those three crash events, which involved starvation deaths as forage became inaccessible nearly range-wide, were disastrous for those populations (Miller et al., 1977a; Miller, 1998; Gunn and Dragon, 2002). There was no indication that the south-central QEI caribou population (or the associated muskox population) had reached or passed through some biologically or ecologically meaningful threshold where a density-dependent response would have had to come into play with subsequent dire results.

Effect of Uneven Caribou Distribution on Bathurst Island

The use of range-wide mean density to evaluate environmental stress on caribou populations characterized by persistent, uneven spatial distribution can be misleading, because it averages the high and low densities that occur on major land areas in different parts of their range. In 1961, Tener (1963), using estimates calculated by survey stratum (Table 3), found that 67% of the land area on Bathurst Island held 99.5% of the estimated caribou and calves represented 20% of all caribou. The observed skewed distribution was 22.1 caribou * 100 [km.sup.-2] on NE Bathurst, 28.9 caribou* 100 km(-2) on NW Bathurst, and only 0.2 caribou* 100 [km.sup.-2] on S Bathurst (Fig. 2). In 1993, when 2273 caribou were actually seen on Bathurst Island alone and 2580 were estimated there, 79% of them were on the NE section, 41% of the island's land area, and calves represented 28% of all caribou. Thus, in 1993 there were 30.6 caribou* 100 [km.sup.-2] on NE Bathurst, but only 8.8 caribou* 100 [km.sup.-2] on NW Bathurst, and 3.6 caribou* 100 [km.sup.-2] on S Bathurst (Table 3). Caribou demands on the forage supply during summer 1993 thus varied by stratum, being 3.5 times greater in the NE than in the NW and 8.5 times greater in the NE than in the S. This highly uneven distribution means that the use of range-wide mean density values to evaluate caribou pressure on the range is questionable, as this method could mask important differences and produce misleading results regarding the actual pressure on forage plants.
TABLE 3. Numbers of Peary caribou (Rangifer torandus pearyi) estimated
by survey stratum on the survey area, south-central Queen Elizabeth
Islands, Canadian High Arctic, 1961 - 97.

Bathurst Island (survey stratum size)

                 Bathurst Island (survey stratum size)

Year (1)  NE (6630 [km.sup.2])  NW (4068 [km.sup.2])  S (5344

1961 (1)         1467                  1177                12

1973              127                   160               425

1974 *            187 *                  44 *               0 *

1981 (3)          160                    70                59

1985              178                   201               116

1988              460                   231               130

1993             2032                   357               191

1996 *            300 *                 131 *              12 *

1997 *             44 *                  20 *              10 *

            Northwestern Satellite Islands (survey stratum size)

          Vanier (1126  Cameron (1059  Alexander (484  Massey (432
          [km.sup.2])   [km.sup.2])    [km.sup.2])     [km.sup.2])

1961 (1)     389           265             187              12

1973          24             9               0              52

1974 *        15 *          20 *             0 *             0 *

1981 (3)          -             -               -            -

1985          67            51              38              76

1988          85             9              31              84

1993        (76) (4)      (30) (4)          70              31

1996 *         9 *           0 *             0 *             0 *

1997 *         0 *           0 *             0 *             4 *

(1) Years in bold are known weather-related die-off years. Population
estimates were made in 1975,1994, and 1995, but not at the stratum

(2) Values of Tener's (1963) 1961 caribou estimates for the five-island
complex were adjusted to correct for the difference in island sizes
used by Tener (1963) and those currently reported in The Atlas of

(3) The August 1981 survey by Ferguson (1987) covered Bathurst Island

(4) Approximated from the mean number of caribou seen in 1985 and 1988
for each island to retain the 19 143 [km.sup.2] survey area in all
survey years.

Caribou performance parameters were high on all three sections of Bathurst Island in 1993, but were highest in the NE, where the density of caribou was also the highest (30.6 caribou* 100 [km.sup.-2]), almost double the mean density for the island as a whole (16.1 caribou* 100 [km.sup.-2]). High population growth throughout the early 1990s, high calf survival, and high representation of yearlings and juveniles all indicate a healthy, fast-growing population, with excellent potential for continued growth in the absence of extremely severe weather years (Tables 4, 5). Thus, there is no evidence to even suggest that whatever kept the population from realizing its full potential directly involved the abundance of its absolute food supply or that it occurred in a density-dependent manner. Had the population responded in a density-dependent manner, it would have experienced a detectable and serious reduction in reproduction and early calf survival, and under especially severe conditions, markedly reduced survival among the l+-yr-old caribou as the population grew larger. Instead, however, the caribou population grew at a mean annual rate of 13%, a high rate of population growth over two decades, even when compared to that of established large populations of North American caribou on much more productive mainland ranges (Messier et al., 1988; Davis and Valkenburg, 1991) and on the island of Newfoundland (Bergerud, 1983).

Density-Dependence Is Not an A Priori Fact of Life

An important question is, why should all observed limitations in reproduction and survival necessarily be interpreted as density-dependent responses? In all likelihood, population productivity could be controlled by a combination of annual and cumulative weather events, either singly or in combination with other factors that are subtle but moderately severe in nature. For example, it is most likely that the effect of reduced forage accessibility would be compounded by different annual rates of wolf predation, which could be quite independent of caribou densities (Valkenburg et al., 1996; Whitten, 1996).

Because of the extreme low growth of vegetation and the patchy appearance of High Arctic caribou ranges, some observers may seriously underestimate forage abundance, leading to speculation that all reductions in population dynamics during the relatively favorable weather years had to be caused by mechanisms operating in a density-dependent manner in response to food limitation. We believe the evidence in this case argues to the contrary. Not all reductions in population size or performance are necessarily triggered by the status of the absolute forage supply or even its accessibility.
TABLE 4. Values describing the population status and performance for
Peary caribou (Rangifer trarandus pearyi) on Bathurst Island and in
its three major survey divisions, south-central Queen Elizabeth
Islands, Canadian High Arctic, in August 1993 (based on 2273 caribou

Statistic           Bathurst     NE Bathurst   NW Bathurst  S Bathurst
                    Island       (6630         (4068        (5344
                    (16042       [km.sup.2]))  [km.sup.2])  [km.sup.2])

l+-yr-old males        69.2          64.4          91.4         80.0
per 100 l+-yr-old

Juveniles (1) and      73.1          71.8          87.0         62.6
yearlings per 100
bulls (2) and
breeding cows (3)

Bulls per 100          43.6          32.9          81.9        130.6
breeding cows

Calves per 100         65.9          69.9          54.7         44.0
l+-yr-old females

Calves per 100         96.8          97.1          97.2         91.7
breeding cows

% calves among all     28.0          29.8          22.2         19.6

% yearlings among   12.1            12.6          10.5         10.1
all caribou

(1) Juveniles are 2-yr-old and some older nonparous females and 2- and
3-yr-old males.
(2) Bulls are considered 4+-yr-old males.
(3) Breeding cows are 3+-yr-old females, but might include some few
primiparous 2-yr-old and even a few yearling females, which would vary
proportionally with the favorableness of the year.

In theory, it is possible that density-dependence could occasionally be important in regulating population growth of Peary caribou on the QEI. However, there are no on-site data from anywhere in the QEI at any time in the past to support this possibility. Also, it is probable that other crash events occurred between 1962 and 1971, a period when the status of the population was unknown. In some years, in the absence of deep snow cover, freezing rain events in early winter (Sep-Oct), late winter (May), or spring (Jun), together with freeze-thaw events and lingering snowmelts, could produce widespread ground-fast ice, ice layering in the snow, or heavy crusting of snow. When widespread or nearly range-wide, these conditions, either singly or in combination, will restrict access to the vegetation for prolonged periods--and many caribou will die (Parker et al., 1975; Miller et al., 1977a; Miller, 1998; Gunn and Dragon, 2002). Thus, it is possible that exceptionally severe widespread icing occurred during some or many of the years from 1961-62 to 1972-73, and that icing alone created lethal conditions for many caribou, even when snow depth was relatively low. Such icing on, in, or under the snowpack would have gone undetected: it was not reported in Arctic weather station records, and no caribou biologists were on site at that time.

The influence of crash years on caribou populations is compounded by those intervening years when calf increments and thus yearling recruitments are lower than average. This is especially true when a near-total loss of the calf crop is accompanied by an increase in deaths among l+-yr-olds. These unpredictable poor calf crop years would also cause serious reduction in the size of the breeding female segment several years later. Therefore, we suggest that if a density-dependent response to the absolute forage supply ever does become the paramount condition for the control of Peary caribou, it would occur--because of the vagaries of the weather and wolf predation--about once a century at most, rather than every few decades. It is only the absence of extremely severe snow or ice conditions, along with wolf populations being below or in balance with their prey base, that allows these Peary caribou populations to experience high growth rates occasionally over a long series of years.

Berryman et al. (2002) concluded that population regulation is merely one of the many behaviors possible in populations of organisms that may or may not occur as a posteriori emergent properties of particular ecological structures, depending on the circumstances. However, White (2001:148) noted that after 60 years of controversy over population regulation, there is still no widespread evidence for it and much evidence against it. He declared a predetermined equilibrium point is a mean, which is "a human construct that does not exist or have any meaning in nature. So how can mortality factors be density-dependent, restoring numbers to something that does not exist?" (White, 2001:150). Krebs (1991:6) concluded that "the density-dependent paradigm is bankrupt because it is descriptive and a posteriori. It does not lead to understanding because no mechanisms are specified. It is an equilibrium-based concept that sheds no light on a non-equilibrium world." Biologists and ecologists, he later added, should "seek mechanisms by which population effects are achieved. Density is not a mechanism" (Krebs, 1995:9).

Density-Independent Factors Operate in a Non-equilibrium Grazing System

Although the Peary caribou population on the south-central QEI experienced an average annual rate of increase of 13.2% for 20 years from 1974 to 1994, 17.7% for the last nine years from 1985 to 1994, and 20.5% for the last six years from 1988 to 1994 (Table 1), there were no reports of range deterioration. When the first year (1994-95) of the three years of annual winter and spring crashes began, and in each of the next two years (1995-96 and 1996-97), the loss of most of the forage supply through inaccessibility was sudden (i.e., within the crash season each year, while the snow or ice cover was still present). The 20 years with relatively favorable weather apparently were too few to allow the Peary caribou, and especially both the Peary caribou and the muskoxen, opportunity to overshoot some unknown, conjecturally critical threshold population size at which the range would have afterwards suffered even serious deterioration, let alone destruction.
TABLE 5. Values deserbing population status and performance for peary
caribou (Rangifer tarandus pearyi) on Bathurst, vanier, Cameron,
Alexander and Massey islands, within a 19 143 [km.sup.2] survey area,
south-central Queen Elizabeth Isalands, Canadian High Arctic, Summers
1990 to 1993, prior to the three consecutive annual crashes in winter
spring 1997-97.

Statistic                         Mean   [++or--]SD    Range

All caribou observed             1462.8    707.4      87 - 2387

l+-yr-old caribou observed       1085.3    473.6     709 - 1720

Calves observed                   377.5    235.6     162 - 667

l+-yr-old males per 100            59.5      6.7      54.5 - 69.1
l+-yr-old females

Juveniles (1) and yearlings per    83.1     16.6      65.6 - 101.6
100 bulls (2) and breeding cows

Bulls per 100 breeding cows        51.9     11.4      41.2 - 65.5

Calves per 100 l+-yr-old           51.9     14.0      35.4 - 65.6

Calves per 100 breeding cows       88.4     10.8      72.6 - 96.7

% calves among all caribou         24.3      4.8      18.6 - 28.6

% yearlings among all caribou      15.2      2.4      13.0 - 18.3

(1) Juveniles are 2-yr-old and some older nonparous females and 2- and
3-yr-old males.

(2) Bulls are considered 4+-yr-old males.

(3) Breeding cows are 3+-yr-old females, but might include some few
primiparous 2-yr-old and even a few yearling females, which would
vary proportionally with the favorableness of the year.

There was no indication of any marked reduction in the annual calf crops from 1991 to 1994, when the population was at its highest densities, but just the opposite: the annual rates of reproduction and calf survival remained high (i.e., in 1991-94, mean percent calves was 26.5% [+ or -] 3.0% SD, range 22.2-28.6%). Also, the minor reliance of Peary caribou on lichens in their seasonal and year-round diets makes it most unlikely that they would experience such a density-dependent condition caused directly by the state of the absolute food supply. Vascular plants--particularly sedges, rushes, and grasses--recover quickly from grazing; some are even stimulated to produce more growth after grazing.

The importance of predation and other limiting factors should not be ignored, nor should a constant state of importance in all things controlling caribou numbers be assumed. There is a suite of controlling factors, and the relative importance of each to the reduction of a caribou population can vary from year to year. However, the extreme weather -related crash experienced by the study population in 1996-97 was so severe that it caused the estimated population of 452 caribou (only 2.4 caribou* 100 [km.sup.-2] of range) to decline by 83% to only 78 animals (0.4 caribou* 100 [km.sup.-2]). Therefore, we believe this extreme level of weather-induced severity occurring at such a low starting mean density within the 19 143 [km.sup.2] five-island area, puts weather--extremely severe snow or ice conditions, abiotic density-independent factors--in the primary position of importance for Peary caribou on the QEI. The post-crash range in summer 1998, the first plant-growing season after the three annual crashes from 1994-95 to 1996-97, appeared adequate to support several thousand caribou (G.H.R. Henry, pers. comm. 1998), a conclusion that is strongly supported by the magnitude of the estimated annual aboveground production of vegetation (Table 2).

We remain confident that the dominant factor controlling the population dynamics of Peary caribou on the southcentral QEI and elsewhere on the QEI has been unfavorable winter or spring weather. In those relatively few years when extremely severe and prolonged snow or ice conditions persisted, the Peary caribou population experienced nearly complete loss of its calf crops and suffered all known major crash events (Parker et al., 1975; Miller et al., 1977a; Miller, 1998; Gunn et al., 2000, 2003; Gunn and Dragon, 2002; Miller and Gunn, 2003a, b). The magnitudes of the 1973-74 single-year crash and the three consecutive winter and spring annual crashes between 1994 and 1997 for both the Peary caribou and the muskox populations appear to be independent of animal or plant density.


Emergent Properties of Forage and Weather

We believe that Peary caribou live in a non-equilibrium grazing system on the QEI where they experience extremely unfavorable stochastic weather events (Gunn et al., 2003; Miller and Gunn, 2003a, b) leading to reduced or failed reproduction, poor early calf survival, and high mortality among l+-yr-old animals. These responses occur at rates that will depend mostly on the frequency, duration, and severity of their exposure to the stressful weather events. The response of the caribou is to a remarkable degree independent of their density (Caughley and Gunn, 1993; Valkenburg et al., 1996; Whitten, 1996; Behnke, 2000). Forage accessibility, rather than animal density, drives changes in Peary caribou populations in an unpredictable manner, and it does so rapidly, causing the extreme severity of the weather-related winter and spring crash events.


These high levels of environmental stochasticity that exist in the High Arctic prevent the vegetation-herbivore feedback loop from becoming a dominant regulating factor for Peary caribou on the QEI. Therefore, long-term fluctuations in these populations are "essentially a mathematical artifact of among year variation in weather, even when the weather exhibits no trend over time" (Caughley and Gunn, 1993:54; see also Behnke, 2000:147). That is, the size of a population at a given time is primarily a function of the size to which the population was last reduced and the number of years with favorable weather that have passed since the last die-off (Valkenburg et al., 1996). Thus, these changes in size of a population caused by environmental fluctuations are largely independent of population size (Figs. 3, 4; Gunn et al., 2003; Miller and Gunn, 2003a, b) and will lead to nearly the same proportionate decrease in numbers whether the population is large or small (Figs. 3, 4; Caughley and Gunn, 1996:170; Behnke, 2000:146). In addition, in the case of Peary caribou on the QEI, this outcome could be altered from time to time by the increasing pressure of wolf predation, especially when the ungulate prey base dwindles from one or more other causes (Gunn et al., 2000).

The exceptionally low growth forms of most of the vegetation on the QEI make it susceptible to being locked down by freezing rain or hard-packed, windblown snow. Such events can occur at snow depths of only 30 cm, or as little as 10 cm, depending on the snow density (compaction) or the coarseness (infiltration qualities) of the substrate. Woo et al. (1982) have shown that because of the hydrological processes involved, ground-fast ice can form under any depth of snow--and even on snow-free sites under certain conditions. The strong correlation between known caribou crashes (Fig. 3) and years with the heaviest total snowfall (Fig. 4) is misleading when accepted intrinsically, as it is only one of several lethal scenarios. We believe that relatively deep snow per se is not necessary to create lethal conditions, but that heavy snowfall does have a greater potential for leading to unfavorable snowpack conditions that are life-threatening. Snow is redistributed by wind action across the range. This redistribution allows wide-spread or range-wide development of extremely severe snow characteristics (i.e., hardness and density) that lead to extreme relative unavailability of the forage for both Peary caribou and muskoxen--and in the worst years, to death by starvation. Also, widespread icing alone, in shallow snow cover or even in the absence of snow cover, can create lethal conditions. Fortunately, in all but the most extreme years, there were either enough areas with favorable snow conditions without the presence of extensive ice, or enough snow-free patches and shallow snow areas free of icing, to allow the caribou to forage without having to dig feeding craters in the hard-packed snow or attempt to do so in the iced-over areas (Miller, 1992, 1993, 1994, 1995b).

The finding by Thomas et at. (1999) that caribou made intensive use of shallow snow or snow-free areas on sparsely vegetated upland ridges where the rush Luzula spp. and lichens were relatively abundant could be misconstrued to mean that lichens constitute the major or a major component of the Peary caribou's diet, which is not the case. Although Peary caribou seek out such sites with shallow or no snow cover, there is no evidence that they consistently use lichens in their diet at much beyond the rate of lichen occurrence on their range. It is therein that the problem lies--lichen growth is slow, and abundance is low in the High Arctic (Klein, 1980; and see the references to this fact given in Miller, 1998:48). Also of great importance, lichens on the QEI virtually do not occur in extensive dense mats like those that foster grazing by caribou on the mainland. Additionally, any food selection on those sites may have been for Luzula, which is an important year-round food item (Thomas et at, 1999).

Lichens are reported as contributing ca. 8% collectively to the plant biomass on Bathurst, Melville, and Prince Patrick islands, and the proportions of lichens in caribou rumen samples from those three islands (10%, 11%, and 2%) were roughly comparable to or well below that level (Thomas and Edmonds, 1983). Lichen cover is sparse on these islands because of the calcareous sedimentary substrates in association with harsh weather (Thomas and Edmonds, 1983). From those findings, it appears that the possible selection for lichens is of minor consequence in terms of the Peary caribou's seasonal and year-round diets. It would be impossible for Peary caribou to have the same strong dependence on lichens that mainland barren-ground caribou (R. t. groenlandicus) have and still live on the QEI.

Bergerud (1996:105) stated that "weather is density independent hence not regulatory" and "weather can only cause death as an interaction since animals don't die directly from exposure, if in good nutrition (and or in the absence of predation)." However, we believe, on the basis of evidence from the QEI, that exceptionally severe weather causes extreme single-year crashes in caribou (and muskox) populations, and that those crashes result from starvation (Gunn et al., 2003; Miller et al., 2005c) and possibly in part from accelerated predation by wolves because killing calves and debilitated prey is quicker and easier (Miller and Broughton, 1974; Miller et al., 1985, 1988). Therefore, we agree with Skoog (1968) that if caribou deaths result from starvation (or predation) caused indirectly by weather conditions, then the controlling factor is the existing weather, and not the wolves or the size or relative accessibility of the absolute food supply (see also Miller, 2003:980). Skoog (1968) concluded that no other factor affects caribou more than the climate, and that weather can hold populations at levels where density-dependent factors are not important. We concur.

Peary Caribou Behavior

Caribou in general are known for their mobility. The caribou of the R. t. pearyi ecotype on the Canadian Arctic Islands exhibit a highly mobile feeding strategy, usually feeding while almost continually on the move (i.e., 2.5-4 Km*[h.sup.-1] while foraging, Miller et al., 1982). They often take only one or, less often, two or three bites of forage from any one position. They seldom spend more that a few minutes on an area, even on large (> 100 [m.sup.2)] snow-free patches, and their time spent at a site is not related to forage richness (Miller et al., 1982; Miller, 1995b). Even caribou coming off the sea ice after making inter-island migrations of 30-84 km (minimum straight-line horizontal distances) and being deprived of food for several hours or more exhibit the same feeding strategy (Miller et al, 1982, 2005b). In contrast, the extensive dense lichen mats and, in general, the more abundant vegetation on mainland ranges allow individual caribou there to feed longer in place or stay on much smaller areas for longer periods of time.

Inter-island populations of caribou have been documented throughout most of the Canadian Arctic Archipelago (Miller, 1990; Miller et al., 2005b). Peary caribou specifically have been documented in the SW eco-unit (Fig. 1; Miller et al., 1977a, b) and in the S-C eco-unit (Fig. 1; Miller, 1995a, 1997, 1998, 2002). Intra-island and inter-island seasonal migrations and in some cases more frequent back-and-forth movements of Peary caribou (Miller, 1995a, 2002; Miller and Barry, 2003) appear to maximize the seasonal use of the best sections of their range and minimize caribou grazing pressure on their winter range (Miller, 1990). Annually switching from winter and spring ranges used during the period of snow cover to different areas of summer range during the snow-free period then back to winter range the next year allows a greater amount of new growth of forage plants on winter ranges during the intervening growing season. Some Peary caribou achieve this same result by seasonal displacements of just a few kilometers or by selecting different micro-sites for foraging on a seasonal basis (Miller and Barry, 2003). Ranges used during the snow-free period of the year are larger than ranges used during the period of snow cover, and the availability, abundance, and quality of the forage supply reach their peak in the middle of the snow-free period.

Is Ka Useful Concept for High Arctic Caribou?

On the basis of the four weather-related crashes, we do not believe that the concept of an ecological carrying capacity (K) is applicable to Peary caribou on the QEI. Carrying capacity cannot be defined or measured with biological confidence only by the highest density ever estimated for a caribou population (MacNab, 1985; Gunn et al., 2000, 2003). An adequate definition would also require measuring the abundance of the absolute food supply. On the QEI, however, this measurement would be sporadically confounded by widespread inaccessible forage. That is, density of the absolute food supply does not matter when sporadic widespread or range-wide extreme snow or ice cover makes the forage inaccessible. Therefore, we suggest that the idea of long-term sustainable harvest of Peary caribou at some satisfactory level is wishful thinking at most, and harvesting these endangered Peary caribou populations, without continually updating their status, is courting disaster. The level of monitoring on the QEI has never been satisfactory for carrying out the biologically sound management and ecologically sound conservation of Peary caribou populations (see Miller et al., 2005a:72-73, for the minimum requirements). It is paramount that responsible parties realize and agree that none of these populations of endangered Peary caribou on the QEI be hunted without first updating their status. The status must be determined by aerial survey each time and the actual number of animals seen--not the number extrapolated--should be used to determine whether the desired harvest is sustainable. The hunters must then restrict their kill to the agreed-upon number or fewer caribou.

Caribou field biologists usually detect reduced population performance and even a marked reduction in population size only well after the fact. Therefore, they often do not have enough details to identify the exact cause and effect (response) that led to poor reproduction, low calf survival, and high mortality among l+-yr-old animals. They often work with the obtainable approximate mean density value for caribou

on the total range, so that they can "tell a story" that may or may not be an accurate account of population dynamics or ecological relationships at a given time or over a period of time. It is common knowledge among caribou field biologists, however, that distributions of caribou are never uniformly even, whether on mainland or on island ranges.

No matter what brought down the Peary caribou population on the south-central QEI to a mere remnant in 1998, it will take at least 30 years at its previous high average annual growth rate of [lambda]- 1.13 under continually favorable weather conditions, and 59 years at half that growth rate ([lambda] = 1.065), to recover to its 3994 size. This vividly illustrates that while population declines can be rapid because mortality has no biological restraints, recovery must be relatively slow because calves can be born and recruited only so fast (Caughley and Gunn, 1993; Whitten, 1996).

A population that persistently approaches or realizes its potential annual maximum level of performance would, in reality, suffer greater setbacks sooner and deeper than a population growing at slow or moderate rates and continually under moderate-to-strong environmental pressure. Caribou biologists need to understand that while shortfalls in reproduction and small-to-moderate increases in mortality among all caribou appear undesirable, such losses caused by ongoing exposure to environmental pressure are actually highly beneficial to the population's well-being over the long run--that is, as long as the population remains in a stable or positive growth phase under existing and future hunting pressure.

For example, a starting population of 10000 animals on a range that would hypothetically support 100000 animals, when experiencing a mean annual growth rate ([lambda]) of 1.05, would reach 100000 animals in ca. 47 years, in the absence of any exceptionally severe weather years. The same population at a high mean annual growth rate ([lambda]. - 1.15) would reach 100000 animals in just ca. 16 years, and at a higher annual growth rate (lambda] = 1.20), in only ca. 13 years. Even the largest of these growth rates is still well below the intrinsic annual maximum rate of increase ([r sub m]- 0.30, Bergerud, 1980), at which rate it would take only nine years to exceed 100000 caribou! Thus the number of years required to reach the maximum 100000 or more caribou is highly variable, depending on the annual rate of growth; it is much less favorable to the population over the long run when this growth happens in only 13-16 years than when it takes nearly half a century. This is particularly true for Peary caribou on the QEI, as the frequency of extreme weather events would most likely double the time necessary (i.e., from 50 to 100 years) to reach a density at which the range could no longer support all of the caribou without a serious impact on the forage plants.

The vagaries of weather in the Canadian High Arctic are such that the number of Peary caribou that the range can support is constantly in a state of flux--by week, month, season, or year. In fact, a range's capacity to support Peary caribou can change drastically within days as a result of one or several severe storms. Extremely unfavorable snow or ice conditions can reduce the number of caribou a range can support from several thousand to several hundred animals or less. However, the capacity to support caribou on this same range will rebound once the snow and ice have melted away.

Thus, we share the frustration in the probable folly of the "cavalier use of the constant K as if it had a precise ecological meaning rather than being simply a mathematical convenience" (Caughley and Gunn, 1996:172). Pimm (1991:136) concluded, while examining models for time to extinction, that "quite what K has to do with real populations is far from obvious" and that he had "no idea whether it [K] exists or how to calculate it." We accept the observation that mathematical models are at best simplistic approximations of the complex real world and that the unrelenting quest for an underlying equilibrium ignores the probability that there might be no equilibrium (Gleick, 1988:59-64). Unfortunately, models also are flexible, and although past data can be fitted to them, these data do not guarantee that the model's predictive power will be accurate or even real. This negative condition could be strongly influenced by the existence of incomputable emergent phenomena (Orrell, 2007:114, 118, 205), which would most likely be common in a non-equilibrium grazing system that is controlled primarily by abiotic weather factors. An important consideration (and probably a major shortcoming in general) is that researchers are not even working with the right factor. To evaluate correctly the capability of a range to support a population of herbivores, the density of the vegetation (forage plants)--not the density of the animals--should be used (Caughley and Gunn, 1993; Whitten, 1996). Even then, such an evaluation of the vegetation would be applicable only when the absolute forage supply was not largely inaccessible.


The Peary caribou study population exhibited high levels of annual reproduction, early calf survival, and low mortality among l+-yr-old animals from 1988 to 1994, when the population estimate tripled from 1030 to 3155 during years of relatively favorable weather. The high levels of population performance and growth of these caribou rival those of much larger established mainland caribou populations with much better forage supplies on ranges with more hospitable environments. It appears that at present, the primary requirement for the well-being of Peary caribou, in the absence of further human interference, is the absence of years with prolonged and extremely severe snow or ice conditions.

We assert that the effects of infrequent, isolated single years or a short series of years with exceptionally severe snow or ice conditions have been the primary control of the study population and, thus, by extension, of Peary caribou populations on the QEI. It is most probable that these abiotic controlling factors were compounded annually by differing levels of wolf predation--a biotic factor. Collectively, the impact of these controlling factors has been too great to allow Peary caribou populations to even reach, let alone exceed, any conjectural equilibrium. There is no evidence, either on site or from anywhere within the QEI, that proves--or even suggests--otherwise.

We remain confident that the four single-year winter and spring crashes were all caused by exceptionally severe and prolonged snow and ice conditions. The pattern of favorable weather years erratically intertwined with less favorable years (with poor reproduction and survival of calves) and a few extremely unfavorable crash years (with nearly no reproduction and disastrous mortality levels) has been in place for centuries and possibly for millennia. Therefore, it is most likely that Peary caribou populations on the QEI would seldom, if ever, reach the sizes (densities) at which density-dependent regulation through negative feedback loops with the absolute forage supply would be the sole or even the primary controlling force. The estimated absolute abundance of aboveground annual plant production relative to the number of caribou estimated on the study area gives credence to our position. We believe this applies in general to Peary caribou populations throughout the QEI, which all occur at relatively low mean densities.

We conclude that large random fluctuations in the environment that occur in the High Arctic prevent the vegetation-herbivore feedback loop from becoming a dominant regulating factor for Peary caribou on the QEI. Those caribou are living in a non-equilibrium grazing system where they are controlled mainly by infrequent, nearly range-wide extremely severe abiotic weather elements--independent of either the caribou density or the abundance of their food supply. Therefore, we propose that the dynamics of a non-equilibrium grazing system with a compounding effect from wolf predation would represent an appropriate conceptual model for Peary caribou populations on the QEI in the Canadian High Arctic.


Most of the studies used herein were supported by the Canadian Wildlife Service, Environment Canada; the Department of Resources, Wildlife and Economic Development, Government of the Northwest Territories; and Parks Canada, Heritage Canada. Polar Continental Shelf Project, Natural Resources Canada, is acknowledged for their longtime logistical support of wildlife studies in the Canadian Arctic. We thank E.S. Telfer, Research Scientist Emeritus, Canadian Wildlife Service, and four anonymous reviewers for their critical reading of earlier versions of the manuscript; their valuable comments and suggestions markedly improved the manuscript. We are especially grateful to W.A. Gould, International Institute for Tropical Forestry, USDA Forest Service, for providing us with tabular vegetation class data for our study area. We also thank M. Raynolds and D.A. Walker, Institute of Arctic Biology, University of Alaska, Fairbanks, for assistance with our search for data sets related to the vegetation maps for our High Arctic Island study area. We also are especially grateful to G.H.R. Henry, Department of Geography, University of British Columbia, for advice and discussions about the vegetation on the study area and for making a detailed review of both the Forage Availability section of the manuscript and Table 2.


Behnke, R.H. 2000. Equilibrium and non-equilibrium models of livestock population dynamics in pastoral Africa: Their relevance to Arctic grazing systems. Rangifer, Special Issue 20(2-3):141-152.

Bergerud, A.T. 1980. A review of the population dynamics of caribou and wild reindeer in North America. In: Reimers, E., Gaare, E., and Skjenneberg, S., eds. Proceedings of the 2nd International Reindeer/Caribou Symposium, Roros, Norway, 1979. Trondheim: Direktoratet for viltog ferkvannsfisk. 556-581.

--. 1983. The natural population control of caribou. In: Bunnell, F.L., Eastman, D.S., and Peek, J.M., eds. Symposium on Natural Regulation of Wildlife Populations. Moscow: Forest, Wildlife and Range Experiment Station, University of Idaho, Proceedings No. 14:14-61

--. 1996. Evolving perspectives on caribou population dynamics, have we got it right yet? Rangifer, Special Issue 9:95-115.

Berryman, A.A., Arce, ML., and Hawkins, B.A. 2002. Population regulation, emergent properties, and a requiem for density dependence. Oikos 99:600-606.

Bliss, L.C. 1990. High Arctic ecosystems: How they develop and are maintained. In: Harington, C.R., ed. Canada's missing dimension: Science and history in the Canadian Arctic Islands, Vol. I. Ottawa, Ontario: Canadian Museum of Nature. 350-384.

Bliss, L.C, and Matveyeva, N.V. 1992. Circumpolar Arctic vegetation. In: Chapin, F.S., III, Jefferies, R.L., Reynolds, J.F., Shaver, G.R., and Svoboda, J., eds. Arctic ecosystems in a changing climate: An ecophysiological perspective. New York: Academic Press. 59-89.

Caughley, G., and Gunn, A. 1993. Dynamics of large herbivores in deserts: Kangaroos and caribou. Oikos 67:47-55.

--. 1996. Conservation biology in theory and practice. Cambridge, Massachusetts: Blackwell. 459 p.

Comiso, J.C. 2002. A rapidly declining perennial ice cover in the Arctic. Geophysical Research Letters 29(20):1956, doi:10.1029/2002GL015650.

Crete, M., Couturier, S., Hearn, B.J, and Chubbs, T.E. 1996. Relative contribution of decreased productivity and survival to recent changes in the demographic trend of the Riviere George caribou herd. Rangifer, Special Issue 9:27-36.

Davis J.L., and Valkenburg, P. 1991. A review of caribou population dynamics in Alaska emphasizing limiting factors, theory, and management implications. In: Butler, C.E, and Mahoney, S.P., eds. Proceedings of the 4th North American Caribou Workshop, St. John's, Newfoundland. 184-209.

Edlund, S. 1990. Bioclimatic zones in the Canadian Arctic Archipelago. In: Harington, C.R., ed. Canada's missing dimension: Science and history in the Canadian Arctic Islands, Vol. 1. Ottawa, Ontario: Canadian Museum of Nature. 421-441.

Edlund, S., and Alt, B. 1989. Regional congruence of vegetation and summer climate patterns in the Queen Elizabeth Islands, Northwest Territories, Canada. Arctic 42(l):3-23.

Ferguson, M.A.D. 1987. Status of Peary caribou and muskox populations on Bathurst Island, N.W.T., August 1981. Arctic 40(2):131-137.

Fischer, C.A., and Duncan, E.A. 1976. Ecological studies of caribou and muskoxen in the Arctic Archipelago and northern Keewatin. Edmonton, Alberta: Renewable Resources Consulting Services Ltd. 194 p.

Gleick, J. 1988. Chaos: Making a new science. New York: Penguin Books. 352 p.

Gould, W.A., Raynolds, M., and Walker, D.A. 2003. Vegetation, plant biomass, and net primary productivity patterns in the Canadian Arctic. Journal of Geophysical Research 108(D2), 8167, doi:10.1029/2001JD000948.

Gunn, A., and Dragon, J. 2002. Peary caribou and muskox abundance and distribution on the western Queen Elizabeth Islands, Northwest Territories and Nunavut June-July 1997. File Report 130. Yellowknife: Northwest Territories Department of Resources, Wildlife and Economic Development, Government of the Northwest Territories. 93 p.

Gunn, A., Miller, F.L., and Nishi, J. 2000. Status of endangered and threatened caribou on Canada's Arctic Islands. Rangifer, Special Issue 12:39-50.

Gunn, A., Miller, F.L., and Barry, S.J. 2003. Conservation of erupting ungulate populations on islands: A comment. Rangifer 23:57-65.

Klein, D. 1980. Range ecology and management: Progress made and directions for the future. In: Reimers, E., Gaare, E., and Skjenneberg, S., eds. Proceedings of the 2nd International Reindeer/Caribou Symposium, Roros, Norway, 1979. Trondheim: Direktoratet for vilt og ferkvannsfisk. 4-9.

Krebs, C.J. 1991. The experimental paradigm and long-term population studies. Ibis 133:3-8.

--. 1995. Two paradigms of population regulation. Wildlife Research 22:1-10.

MacNab, J. 1985. Carrying capacity and related slippery shibboleths. Wildlife Society Bulletin 13:403-410.

Maxwell, B. 1981. The climatic regions of the Canadian Arctic Islands. Arctic 34(3):225-240.

--. 1997. Responding to global climate change in Canada's Arctic. Downsview, Ontario: Environment Canada. 82 p.

Messier, F., Huot, J., Le Henaff, D., and Luttich, S. 1988. Demography of the George River caribou herd: Evidence of population regulation by forage exploitation and range expansion. Arctic 41(4):279-287.

Miller, F.L. 1987. Peary caribou and muskoxen on Bathurst, Alexander, Marc, Massey, Vanier, Cameron, Helena, Lougheed, and Edmund Walker islands, Northwest Territories, July 1985. Canadian Wildlife Service Technical Report Series 20. 45 p.

--. 1989. Reevaluation of the status of Peary caribou and muskox populations within the Bathurst Island complex, Northwest Territories, July 1988. Canadian Wildlife Service Technical Report Series 78. 86 p.

--. 1990. Inter-island movements of Peary caribou: A review and appraisement of their ecological importance. In: Harington, C.R., ed. Canada's missing dimension: Science and history in the Canadian Arctic Islands, Vol. 2. Ottawa, Ontario: Canadian Museum of Nature. 608-632.

--. 1991. Peary caribou calving and postcalving periods, Bathurst Island complex, orthwest Territories, 1989. Canadian Wildlife Service Technical Report Series 118. 72 p.

--1992. Peary caribou calving and postcalving periods, Bathurst Island complex, Northwest Territories, 1990. Canadian Wildlife Service Technical Report Series 151. 87 p.

--. 1993. Peary caribou calving and postcalving periods, Bathurst Island complex, Northwest Territories, 1991. Canadian Wildlife Service Technical Report Series 166. 99 p.

--. 1994. Peary caribou calving and postcalving periods, Bathurst Island complex, Northwest Territories, 1992. Canadian Wildlife Service Technical Report Series 186. 99 p.

--. 1995a. Inter-island water crossings by Peary caribou, south-central Queen Elizabeth Islands. Arctic 48(1):8-12.

--. 1995b. Peary caribou studies, Bathurst Island complex, Northwest Territories, July-August 1993. Canadian Wildlife Service Technical Report Series 230. 76 p.

--. 1995c. Status of wolves on the Canadian Arctic Islands. In: Carbyn, L.N., Fritts, S.H., and Seip, D.R., eds. Ecology and conservation of wolves in a changing world. Canadian Circumpolar Institute, Occasional Publication 35:35-42.

--. 1997. Peary caribou conservation studies, Bathurst Island complex, Northwest Territories, April-August 1994 and June-July 1995. Canadian Wildlife Service Technical Report Series 295. 155 p.

--. 1998. Status of Peary caribou and muskox populations within the Bathurst Island complex, south-central Queen Elizabeth Islands, Northwest Territories, July 1996. Canadian Wildlife Service Technical Report Series 317. 147 p.

--. 2002. Multi-island seasonal home range use by two Peary caribou, Canadian High Arctic Islands, Nunavut, 1993-94. Arctic 55(2):133-142.

--. 2003. Caribou Rangifer tarandus. In: Feldhamer, G.A., Thompson, B.C., and Chapman, J.A., eds. Wild mammals of North America: Biology, management, and conservation. Baltimore, Maryland: John Hopkins University Press. 965-997.

Miller, F.L., and Barry, S.J. 2003. Single-island home range use by four female Peary caribou, Bathurst Island, Canadian High Arctic, 1993-94. Rangifer, Special Issue 14:267-281.

Miller, F.L., and Broughton, E. 1974. Calf mortality on the calving grounds of the Kaminuriak caribou. Canadian Wildlife Service Report Series 26. 26 p.

Miller, F.L., and Gunn, A. 2003a. Catastrophic die-off of Peary caribou on the western Queen Elizabeth Islands, Canadian High Arctic. Arctic 56(4):381 - 390.

--. 2003b. Status, population fluctuations and ecological relationships of Peary caribou on the Queen Elizabeth Islands: Implications for their survival. Rangifer, Special Issue 14: 213-226.

Miller, F.L., and Reintjes, F.D. 1995. Wolf-sightings on the Canadian Arctic Islands. Arctic 48(4):313-323.

Miller, F.L., Russell, R.H., and Gunn, A. 1977a. Distributions, movements and numbers of Peary caribou and muskoxen on western Queen Elizabeth Islands, Northwest Territories, 1972-74. Canadian Wildlife Service Report Series 40. 53 p.

--. 1977b. Interisland movements of Peary caribou (Rangifer tarandus pearyi) on western Queen Elizabeth Islands, Arctic Canada. Canadian Journal of Zoology 55:1029-1037.

Miller, F.L., Edmonds, E.J., and Gunn, A. 1982. Foraging behaviour of Peary caribou in response to springtime snow and ice conditions. Canadian Wildlife Service Occasional Paper 48. 41 p.

Miller, F.L., Gunn, A., and Broughton, E. 1985. Surplus killing as exemplified by wolf predation on newborn caribou. Canadian Journal of Zoology 63:295-300.

Miller, F.L., Broughton, E., and Gunn, A. 1988. Mortality of migratory barren-ground caribou on the calving grounds of the Beverly herd, Northwest Territories, 1981 - 83. Canadian Wildlife Service Occasional Paper 66. 26 p.

Miller, F.L., Barry, S.J., and Calvert, W.A. 2005a. Conservation of Peary caribou based on a recalculation of the 1961 aerial survey on the Queen Elizabeth Islands, Arctic Canada. Rangifer, Special Issue 16:65 - 75.

--. 2005b. Sea-ice crossings by caribou in the south-central Canadian Arctic Archipelago and their ecological importance. Rangifer, Special Issue 16:77 - 88.

--. 2005c. St. Matthew Island reindeer crash revisited: Their demise was not nigh--but then, why did they die? Rangifer, Special Issue 16:185 - 197.

Orrell, D. 2007. Apollo's arrow. Toronto, Ontario: Harper Perennial. 449 p.

Parker, G.R., Thomas, D.C., Broughton, E., and Gray, D.R. 1975. Crashes of muskox and Peary caribou populations in 1973 - 74 in the Parry Islands, Arctic Canada. Canadian Wildlife Service Progress Notes 56. 10 p.

Pimm, S.L. 1991. The balance of nature? Chicago, Illinois: The University of Chicago Press. 434 p.

Skoog, R.O. 1968. Ecology of the caribou (Rangifer tarandus granti) in Alaska. Dissertation, University of California at Berkeley, Berkeley. 699 p.

Slaney, F.F. 1975. Peary caribou and muskoxen and Panarctic's seismic operations on Bathurst Island, N.W.T. 1974. Vancouver, British Columbia: Unpubl. report prepared for Panarctic Oils Ltd. by F.F. Slaney and Co. Available from Environment Canada Library, Room 200, Twin Atria Bldg., 4999-98 Avenue NW, Edmonton, Alberta T6B 2X3. 78 p.

Tener, J.S. 1963. Queen Elizabeth Islands game survey, 1961. Canadian Wildlife Service Occasional Paper 4. 50 p.

Thomas, D.C. 1982. The relationship between fertility and fat reserves of Peary caribou. Canadian Journal of Zoology 60:597-602.

Thomas, D.C, and Edmonds, E.J. 1983. Rumen contents and habitat selection of Peary caribou in winter, Canadian Arctic Archipelago. Arctic and Alpine Research 15:97-105.

Thomas, D.C, Edmonds, E.J., and Armbruster, H.J. 1999. Range types and their relative use by Peary caribou and muskoxen on Melville Island, NWT. Canadian Wildlife Service Technical Report Series 343. 146 p.

Valkenburg, P., Davis, J.L., Ver Hoef, J.M., Boertje, R.D., McNay, M.E., Eagan, R.M., Reed, D,J., Gardner, C.L., and Tobey, R.W. 1996. Population decline in the Delta caribou herd with reference to other Alaskan herds. Rangifer, Special Issue 9: 53-62.

Weller, G. 2000. The weather and climate of the Arctic. In: Nuttall, M., and Callaghan, TV., eds. The Arctic environment, people, policy. Amsterdam: Hardwood Academic Publishers. 143-160.

White, T.C.R. 2001. Opposing paradigms: Regulation or limitation of populations? Oikos 93:148- 152.

Whitten, K.R. 1996. Ecology of the Porcupine caribou herd. Rangifer, Special Issue 9:45-51.

Woo, M.-K., Heron, R., and Marsh, P. 1982. Basal ice in High Arctic snowpacks. Arctic and Alpine Research 14: 251 -260.


(1) 14319 - 106B Avenue NW, Edmonton, Alberta T5N 1G1, Canada;

(2) 1223 - 85 Street NW, Edmonton, Alberta T6K 1X7, Canada

[C] The Arctic Institute of North America

(Received 12 May 2008; accepted in revised form 21 July 2008)
COPYRIGHT 2009 Arctic Institute of North America of the University of Calgary
No portion of this article can be reproduced without the express written permission from the copyright holder.
Copyright 2009 Gale, Cengage Learning. All rights reserved.

Article Details
Printer friendly Cite/link Email Feedback
Author:Miller, Frank L.; Barry, Samuel J.
Article Type:Report
Geographic Code:0ARCT
Date:Jun 1, 2009
Previous Article:Adapting to climate change in the southwest Yukon: locally identified research and monitoring needs to support decision making on sustainable forest...
Next Article:Population dynamics of long-tailed ducks breeding on the Yukon-Kuskokwim Delta, Alaska.

Terms of use | Privacy policy | Copyright © 2019 Farlex, Inc. | Feedback | For webmasters