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The observations of naturalists and explorers have been used as historical sources for determining baseline wildlife conditions from the earliest practice of modern ecology. These sources are rarely critically analyzed, however, and are often incorporated into contemporary scientific literature advocating the conservation and restoration of wildlife. This essay argues that combining approaches from environmental history and recent ecological research will allow for the interrogation of original sources and the application of scientific concepts that questions the assumptions underlying historical baselines.
Once there were so many: Animals as Ecological Baselines
Yolanda F. Wiersma (corresponding author)
Department of Biology
Memorial University of Newfoundland
St. John’s, NL
tel: 709-864-7499
John Sandlos
Department of History
Memorial University of Newfoundland
St. John’s, NL
A1C 5S7
tel: 709-864-2429
Once there were so many: Animals as Ecological Baselines
Yolanda F. Wiersma and John Sandlos
The observations of naturalists and explorers have been used as historical sources for
determining baseline wildlife conditions from the earliest practice of modern ecology.
These sources are rarely critically analyzed, however, and are often incorporated into
contemporary scientific literature advocating the conservation and restoration of wildlife.
This paper argues that combining approaches from environmental history and recent
ecological research will allow for the interrogation of original sources and the application
of scientific concepts that questions the assumptions underlying historical baselines.
Peter Matthiessen’s Wildlife in America was one of the first popular books to provide a
comprehensive account of the staggering population declines of North American fauna
since the arrival of Europeans. Drawing on the field notes and papers of natural
historians, Matthiessen invokes images of pre-contact North American wildlife
abundance and subsequent declines as a prelude to his call for restoration of the most
critically endangered species. Similarly, more recent proponents of large-scale wildlife
restoration programs almost inevitably invoke past images of pre-contact wildlife super-
abundance to justify their initiatives. Where once large animals numbered in the
millions, they suggest, now only thousands or even hundreds of individuals have
survived the cumulative impacts of European settlement. Thus, historical wildlife
population estimates are used to justify ambitious wildlife restoration projects, since they
provide a baseline against which to measure the destruction of nature and loss of
biodiversity at human hands.
But where do the baseline numbers for pre-contact fauna come from? Typically,
the early twentieth-century naturalists and conservationists who first calculated historical
wildlife populations relied on rudimentary accounts of earlier explorers, geologists and
surveyors. Using these visual accounts of bison, elk, and antelope (or, in the absence of
these, using contemporaneous data from the same region on the density of domestic
livestock) early naturalists then extrapolated this number over an estimated historical
range. Ernest Thompson Seton adopted this technique throughout his influential multi-
volume 1927 study, The Lives of Game Animals. To calculate pre-contact bison
numbers, for example, Seton used data on horse and cattle densities to produce a
figure of sixty-five million animals. He then refined this number using the visual herd
estimates of early observers, extrapolating these numbers across the total historical
bison range in North America to produce a “safe estimate” of sixty million animals.
Using similar methods, Seton painted a fantastic portrait of bygone North America
teeming with wildlife: forty-five million antelope, forty million white tailed deer, ten million
mule deer, ten million elk, two million bighorn sheep, one million moose, and one million
wolves, all in addition to the unimaginable numbers of bison.
The uncritical adoption of such speculative historical population baselines can
produce unrealistic goals within contemporary wildlife restoration projects. In the case of
the wood bison subspecies in northern Canada, for instance, a pre-contact estimate of
168,000 animals is often cited as justification for restoring seed populations throughout
their estimated historical range. This number first appeared in a report that the
Canadian government biologist J. Dewey Soper issued in 1941. As with Seton, Soper
arrived at this figure by citing several explorers’ accounts of “very plentiful” herds in the
Slave and Peace River ranges and extrapolating current estimates of the bison
population in Wood Buffalo National Park across an assumed historical range. Although
the Canadian government’s current recovery plan does not specify an absolute return to
168,000 wood bison as a primary goal, this number is often invoked as justification for
stocking the species throughout all areas within its presumed historical range.
approach to wood bison recovery has proceeded without asking whether the sightings
of “very abundant” herds were spread evenly throughout the historic wood bison range,
or whether explorers travelling along the Peace River were not seeing plains bison at
the edge of their range. Without such background information, can we be certain that
the wood bison population prior to European contact consisted of more than a few
thousand animals clinging to a sparse existence at the far edge of suitable habitat on
this continent?
Despite their shortcomings, the speculative population estimates of early wildlife
scientists continue to be incorporated in some peer-reviewed scientific literature and
remain influential as credible baseline numbers. It is remarkable in particular how
Seton’s population guesswork on species such as bison, bighorn sheep, elk, and
wolves has been transmitted from the older literature to very recent scientific papers
outlining local restoration projects for these species.
Even simple errors, such as the
gradual adoption of the wrong measurement units for the baseline prairie dog range
one hundred hectares rather than the correct figure of one hundred acrescan work
their way from publication to publication and influence restoration initiations.
At the very
least, it is clear that some contemporary observers derive their baseline figures without
a critical examination of original sources, transmitting extremely speculative population
figures from one publication to the next.
With a disciplinary training devoted to the critical examination of historical
sources, much more could be done to integrate environmental history perspectives with
contemporary attempts to re-wild portions of North America. But the deficiencies in
historical data sets should only be a starting point for this discussion. Taken to its logical
extreme, such critical analysis can leave us with no basis on which to determine
historical patterns of wildlife distribution and abundance. Indeed, questions about
baseline population or range size are not unanswerable; historians have much to learn
from emerging ideas and techniques that contemporary ecologists have used to assess
historical wildlife populations and habitats.
Many of the sources ecologists use to assess historical wildlife range and
abundance are familiar to historians: museum collections, archival material, land survey
records, and oral history. In one study of the Florida grouper, for example, scientists
used newspaper accounts and archival photographs detailing catch totals and the size
of individual fish to estimate historical population fluctuations.
Ecologists have also
assembled historical population estimates using sources and methods that are less well
known to traditional historians, such as herbarium records, genetic analyses, sediment
cores, zooarchaelogical records, and tree ring records.
On a more abstract level, some
ecologists have argued that remnant landscapes retaining a close resemblance to
conditions in specific historical periods (most notably protected areas) may serve as a
source of historical ecological data, a technique known as space-for-time-substitutions.
None of these sources and analytical techniques provides an absolutely precise
window on historical wildlife populations at a particular moment of time. Indeed, most
ecologists readily acknowledge that ecological systems are not static: historical
management interventions may have so profoundly altered conditions even in protected
areas, or animal populations may have fluctuated so dramatically over time, that they
must be analyzed within a concept known as the historical range of variability. Some
techniques, such as tree-ring and sediment core analyses, explicitly measure some of
the variability in species abundance and ecological conditions through time. In other
cases where data are lacking or suspect, scientists must use modeling techniques to
determine the historical range of variability. Often this is done by back-casting, a
mathematical modeling technique that uses current data on demographic rates
(survival, reproduction) and population densities in different habitat types to estimate
historical population sizes. As Alagona (this issue) suggests, the fundamental link
between habitat change and critically engendered wildlife has been recognized for
some time. Thus, ecologists have often used current and historical landscape data
(from satellite images, air photos and maps) and land change data (which can be
complemented by archival records that document land use) to model historical land
cover and habitat types. These data can then be used to estimate historical populations
of species based on contemporary densities in different habitat types.
Obviously, these techniques will always retain a degree of uncertainty. Most
importantly, variations in the model inputs (i.e., which values of reproduction or survival
from current populations are used) can affect final population estimates. In addition,
while contemporary ecologists use more robust data sets than did Seton, they still face
the basic methodological problem of estimating historical wildlife populations based on
contemporary conditions that may be considerably altered. To deal with this uncertainty,
ecologists often conduct a sensitivity analysis, simulating different levels of inter-annual
variation in survival and reproduction through time and seeing how much the baseline
population estimates vary. This method explicitly rejects the idea of singular historical
population estimates, instead modeling the historical range of variability in a manner
that gives scientists a probable set of values for baseline populations.
Ecologists have also evaluated the problem of locating a baseline population at a
particular moment in time. As with environmental historians, many ecologists have
questioned simplistic assumptions that baseline wildlife populations in North America
are inherently tied to the pre-contact period. Studies of upland birds in New England
suggested, for example, that populations increased from pre-European levels coincident
with agricultural expansion. Major declines in upland bird populations only began in the
twentieth century after reforestation that followed the abandonment of agricultural land
reclaimed suitable meadow habitats. A more recent study modeled the effects of culling
bison in enclosed reserves to mimic historical levels of predation by wolves and
indigenous hunters in an effort to keep bison at simulated baseline densities. The
authors concluded that the North America bison population was probably closest to
baseline conditions prior to widespread Native American use of horses in the
seventeenth century rather than the more commonly cited period of westward
expansion in the nineteenth century.
Clearly, locating a population baseline at a particular moment in time presents an
immense methodological challenge. As Barrow argues elsewhere in this issue, the fluid
nature of animal populations might prompt some to question whether it is even possible
to quantify a baseline animal population within a specific time period. But historians and
ecologists have largely abandoned the concept of static and singular baseline numbers
for pre-contact wildlife, using an array of methods that can quantify historical ranges and
fluctuations in animal populations. Working together, historians can lead scientists to
new sources of archival material and interpret historical data within broader histories of
regional environmental change while ecologists can contribute to historical knowledge
though applied analytical techniques that may verify or serve as a powerful corrective to
assumptions about wildlife populations in published and archival sources. Both forms of
knowledge are essential in the policy realm, providing a more nuanced analysis of
historical wildlife population estimates that currently guide many wildlife and habitat
restoration programs.
Thanks to Peter Alagona for the invitation to participate in this forum and to fellow forum participants for
insightful comments. Thanks also to Nancy Langston and two anonymous reviewers for helpful feedback
on an earlier version of the manuscript.
Yolanda F. Wiersma is an Assistant Professor of Biology at Memorial University of Newfoundland. Her
research interests are in Landscape Ecology, Wildlife Ecology and Conservation Biology in the Canadian
boreal region. John Sandlos is an Associate Professor of History at Memorial University of Newfoundland.
His research is focused on wildlife issues and abandoned mines in northern Canada.
For an overview of wildlife restoration initiatives, see David S. Maeher, Reed F. Noss and Jeffry L. Larkin, Large Mammal
Restoration: Ecological and Sociological Challenges in the 21
Century (Washington: Island Press, 2001).
See Ernest Thompson Seton, Lives of Game Animals, An Account of those Land Animals in America North of the Mexican
Border, which are considered “Game,” either because they have held the Attention of Sportsmen, or received the Protection of
Law, Volume 3, Part 1-2, (Boston: Charles T. Branford, Company, 1953), 655-56.
J. Dewey Soper, “History, Range and Home Life of the Northern Bison,” Ecological Monographs 2 (Oct. 1941): 362. Soper’s
estimate is cited in the following publications: National Wood Bison Recovery Team, National Recovery Plan for the Wood
Bison (Bison bison athabascae). National Recovery Plan No. 21 (Ottawa: Environment Canada, 2001); William Harper and
Cormack Gates, “Recovery of Wood Bison in British Columbia,” in L.M. Darling, ed. 2000. Proceedings of a Conference on the
Biology and Management of Species and Habitats at Risk, Kamloops, B.C., Volume Two B.C. Ministry of Environment, Lands
and Parks, Victoria, B.C. and University College of the Cariboo, Kamloops, B.C. (15-19 Feb.,1999), 915; British Columbia
Ministry of Water, Land and Air Protection, Wildlife at Risk in British Columbia Wood Bison. (accessed Nov. 27, 2009), 1.
Using article index Scopus, we found the following 19 papers in the peer reviewed scientific literature (dates ranging from 1936
to 2007) that cited Seton’s population estimates as a credible baseline for various mammal populations. For citations of Seton’s
bighorn (or mountain) sheep estimates, see Helmut K. Buechner, “the Bighorn Sheep in the United States,” Wildlife Monographs
4 (May 1960): 3-174; Fred Mallery Packard, “An Ecological Study of the Bighorn Sheep in Rocky Mountain National Park,
Colorado,” Journal of Mammalogy 27 (February 1946): 3-28; Lester J. McCann, “Ecology of the Mountain Sheep,” American
Midland Naturalist 56 (October 1956): 297-324; Gustavo A. Gutierrez-Espelata, Philip W. Hedrick, Steven T. Kalinowski,
Daniel Garrigan, Walter M. Boyce, “Is the Decline of Desert Bighorn Sheep from Infectious Disease the Result of Low MHC
Variation?Heredity 86 (2001): 439-450; Paul R. Krausman, Peter Bangs, Kyran Kunkel, Michael K. Phillips, Zack Parsons, and
Eric Rominger, “Mountain Sheep Restoration through Private/Public Partnership,Large Mammal Restoration, 231;. For
references to Seton’s elk estimates, see Jeffery L. Larkin, Roy A. Grimes, Louis Cornicelli, John J. Cox, and David S. Maehr,
“Returning Elk to Appalachia, Foiling Murphy’s Law,” Large Mammal Restoration, 101; Jason F. Hicks, Janet L. Rachlow, Olin
E. Rhodes, Jr., Christen L. Williams, Lisette P. Waits, “Reintroduction and Genetic Structure: Rocky Mountain Elk in
Yellowstone and the Western States,Journal of Mammalogy 88 (2007): 129-38; Rick Rosatte, Joe Hamr, Jim Young, Ivan
Filion, Howard Smith, “The Restoration of Elk (Cervus elaphus) in Ontario, Canada: 1998-2005,Restoration Ecology 15
(March 2007): 34-43. For references to Seton’s estimates for wolves, see C. Vilà, R. Amorim, J.A. Leonard, D. Posada, J.
Castroviejo, F. Petrucci-Fonsesca, K.A. Crandall, H. Ellegren, R.K. Wayne, “Mitochondrial DNA Phylogeography and
Population History of the Grey Wolf Canis lupus,” Molecular Ecology 8 (1999): 2089-2103; Jennifer A. Leonard, Carles Vilà,
Robert K. Wayne, “Legacy Lost: Genetic Variability and Population Size of Extirpated US Grey Wolves (Canis lupus),”
Molecular Ecology 14 (2005): 9-17. Seton’s bison estimate has been revised downwards: see Natalie Dierschke Halbert, “The
Utilization of Genetic Markers to Resolve Modern Management Issues in Historic Bison Populations: Implications for Species
Conservation,” (PhD Dissertation, Texas A&M University December 2003), 3. But even with this downward revision of bison
numbers, Seton’s estimate is often mentioned as the upper end of a historical range of estimates. See Floyd Larson, “The Role
Bison in Maintaining the Short Grass Plains,Ecology 21 (April 1940): 113-121; George Arthur, “The North American Plains
Bison: A Brief History,Prairie Forum 9 (Winter 1984): 282; Frank Camp, “The Tragedy of the American Buffalo,” Canadian
West 6 (1990): 126; Judit L. McDonald, “Essay: Bison Restoration in the Great Plains and the Challenge of their Management,”
Great Plains Research 11 (Spring 2001): 104. For more isolated references to Seton’s estimates of other species, see James Beer,
“Distribution and Status of Pronghorn Antelope in Montana,” Journal of Mammalogy 25 (February 1944): 43-46; Daniel W.
Mulhern and Craig J. Knowles, “Black-Tailed Prairie Dog Status and Future Conservation Planning,” Conserving Biodiversity on
Native Rangelands, Symposium Proceedings, August 17, 1995, Fort Robinson State Park, Nebraska (Fort Collins, CO: U.S.
Department of Agriculture, Forest Service, Rocky Mountain Forest and Range Experiment Station), 19-29; Robert J. Naiman,
Jerry M. Melillo, John E. Hobbie, “Ecosystem Alteration of Boreal Forest Streams by Beaver (Castor Canadensis),Ecology 67
(October 1986): 1254-69; Robert J. Naiman, Carol A. Johnston, James C. Kelley, “Alteration of North American Streams by
Beaver,” Bioscience 38 (December 1988): 753-62. Seton’s populations estimates of bison, antelope, white-tailed deer, elk, and
mule deer were all cited Frederic E. Clements’ famous discussion of successional climax. See Clements, “Nature and Structure of
the Climax,” Journal of Ecology 24 (February 1936): 252-84. The authors have also encountered high numbers of references to
Seton in the popular natural history literature and in government reports. For the prairie dog example see, Lance T. Vermeire,
Rod K. Heitschmidt, Patricia S. Johnson, Bok F. Sowell “The Prairies Dog Story: Do we Have it Right?” BioScience 54 (July
2004): 689-95.
Loren McClenachan, “Historical Declines of Goliath Grouper Populations in South Florida, USAEndangered Species
Research 7 (2009): 175-81. For other archival studies, see Richard B. King, Michael J. Oldham, Wayne F. Weller, Douglas
Wynn. “Historic and Current Amphibian and Reptile Distributions in the Island Region of Western Lake Erie,” American
Midland Naturalist 138 (July 1997): 153-73. See also Mark Madison, “Conserving Conservation: Field Notes from an Animal
Archive,” The Public Historian 26 (Winter 2004): 145-55. For studies using land survey data, see Andrew P. Rayburn and
Annabel L. Major, “Using Landscape History and Baseline Data in the Restoration of a Midwestern Savanna,” Journal of the
Iowa Academy of Science 115 (2008): 1-11. A summary of the use and limitations of survey data for ecological work can be
found in L.A. Shulte and D. J. Mladenoff, “The Original US Public Land Survey Records: their use and Limitations in
Reconstructing Presettlement Vegetation,” Journal of Forestry 99 (2001): 5-10.
For genetic analysis, see M.K. Schwartz, K.B. Aubry, K.S. McKelvey, K.L. Pilgrim, J.P. Copeland, J.R. Squires, R.M. Inman,
S.M. Wisely and L.F. Ruggiero, “Inferring Geographic Isolation of Wolverines in California Using Historical DNA,Journal of
Wildlife Management 71 (2007): 2170-79. For sediment cores, see Frank E. Marshall III, G. Lynn Wingard and Patrick Pitts, “A
Simulation of Historic Hydrology and Salinity in Everglades National Parks: Coupling Paleoecologic Assemblage Data with
Regression Models,” Estuaries and Coasts 32 (2009): 37-53. For a zooarchaeological study, see Maribeth S. Murray,
“Zooarchaeology and Arctic Marine Mammal Biogeography, Conservation and Management,” Ecological Applications 18
(2008): S41-S55. For tree ring data, see Lee E. Frelich and Craig G. Lorimer, “Natural Disturbance Regimes in Hemlock-
hardwood Forests of the Upper Great Lakes Region,” Ecological Monographs 61 (1991): 145-64.
See P. Arcese and A.R.E. Sinclair, “The Role of Protected Areas as Ecological Baselines,” Journal of Wildlife Management 61
(1997): 587-602; A.R.E. Sinclair, Simon A.R. Mduma and Peter Arcese, “Protected Areas as Biodiversity Benchmarks for
Human Impact: Agriculture and the Serengeti Avifauna,” Proceedings of the Royal Society London, Series B. 269 (2004): 2401-
For critiques of protected areas as baselines for ecological change, see G.E. Davis, D.M. Graber and S.A. Acker, “National
Parks as Scientific Standards for the Biosphere; Or, how are you going to tell how it used to be, when there’s nothing left to see?
The George Wright Forum 21 (2004): 34-44; T. Josefsson, G. Hörnberg, L. Östlund, “Long-term Human Impact and Vegetation
Changes in a Boreal Forest Reserve: Implications for the use of Protected Areas as Ecological ReferencesEcosystems 12
(2009): 1017-36. For an explanation of historical range of variability, see Peter B. Landres, Penelope Morgan, Frederick J.
Swanson, “Overview of the use of Natural Variability Concepts in Managing Ecological Systems” Ecological Applications 9
(1999): 1179-88; Gregory H. Aplet and William S. Keeton, “Application of Historical Range of Variability Concepts to
Biodiversity Conservation.” In Practical Approaches to the Conservation of Biological Diversity, Richard K. Baydack, Henry
Campa, Jonathan B. Haufler, eds. (Washington: Island Press, 1999), 71-86. For a discussion of back-casting, see H. Kokko, E.
Helle, J. Lindström, E. Ranta, T. Sipliä, F. Courchamp, “Backcasting Population Sizes of Ringed and Grey Seals in the Baltic and
Lake Saimaa During the 20
CenturyAnnales Zoologici Fennici 36 (1999): 65-73. For modeling historical habitat change see
Etouko Nonaka, Thomas A. Spies, Historical Range of Variability in Landscape Structure: a Simulation Study in Oregon,
USA,” Ecological Applications 15 (2005): 1727-46.
For example see A.R. Hoelzel, J. Halley, S.J. O’Brien, C. Campagna, T. Arnborm,, B. LeBoeuf, K. Ralls, G.A. Dover,
“Elephant Seal Genetic Variation and the use of Simulation Models to Investigate Historical Population Bottlenecks” The
Journal of Heredity 84 (1993): 443-9; Hans J. Skuag, Lennnart Frimannslund, Nils I. Øien, “Historical Population Assessment of
Barents Sea Harp Seals (Pagophilus groenlandicus),” ICES Journal of Marine Science 64 (2007): 1356-65.
For the upland bird study, see David R. Foster, Glenn Motzkin, Debra Bernardos, James Cardoza, “Wildlife Dynamics in the
Changing New England Landscape,” Journal of Biogeography 29 (2002): 1337-57. For the bison study, see Joshua J.
Millspaugh, Robert A. Gitzen, Daniel S. Licht, Sybill Amelon, Thomas W. Bonnot, David S. Jachowshi, D. Todd Jones-Farrand,
Barbara J. Keller, Conor P. McGowan, M. Shane Pruett, Chadwick D. Rittenhouse, Kimberly M. Suedkamp Well, “Effects of
Culling on Bison Demographics in Wind Cave National Park, South Dakota,Natural Areas Journal 28 (2008): 240-50. For a
historical treatment of this issue, see Andrew Isenberg, The Destruction of the Bison (Cambridge: Cambridge University Press,
... In contrast to this perspective, however, an awareness of potential error (overestimation) associated with historical baseline population or range size estimates is needed when considering restoration targets. Issues around the reliability of, and guesswork in, the historical methods used to determine estimates have been raised (Wiersma and Sandlos 2011). The concern is that the repeated transmission of historical speculative figures of abundance and/or range size through time could raise unrealistic expectations for environmental management and restoration efforts. ...
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Translocation is a common tool for restoring wildlife populations; however, potential genetic consequences include reduced levels of diversity within and increased divergence among populations. Elk (Cervus elaphus) were extirpated across much of North America by the early 20th century, but subsequent translocation programs restored the species to much of its historic range. The effects of these reintroductions on current patterns of genetic diversity in the western United States are largely unknown. We predicted that populations initiated with few founders and those experiencing slow postreintroduction growth would exhibit lower levels of diversity than other reintroduced populations. We used 12 microsatellite markers to examine patterns of genetic variability across 5 reintroduced populations of elk and 2 source herds from the Greater Yellowstone Ecosystem. The northern and southern Yellowstone source herds, which migrate to wintering areas separated by more than 260 km, exhibited similar levels of genetic diversity and high levels of gene flow, identified through both direct (i.e., assignment tests) and indirect measures. Levels of genetic diversity also were relatively high in all populations (unbiased heterozygosity, HE = 0.51–0.60; allelic richness based on a sample size of 21, AR21 = 3.3–4.0) and did not differ significantly between source and reintroduced populations or among reintroduced populations. We observed low to moderate levels of differentiation (Weir and Cockerham's FST statistic, θ = 0.01–0.08) and small genetic distances (Nei's standard genetic distance, DS = 0.02–0.11) between populations. The relatively high levels of genetic diversity and low differentiation observed among our sampled populations are in stark contrast to observations of low diversity and high differentiation among isolated reintroduced populations of elk in the eastern United States. These results suggest that gene flow that includes other elk populations in the western United States may aid in preserving genetic diversity and limiting genetic divergence.
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Natural resource managers have used natural variability concepts since the early 1960s and are increasingly relying on these concepts to maintain biological diversity, to restore ecosystems that have been severely altered, and as benchmarks for assessing anthropogenic change. Management use of natural variability relies on two concepts: that past conditions and processes provide context and guidance for managing ecological systems today, and that disturbance-driven spatial and temporal variability is a vital attribute of nearly all ecological systems. We review the use of these concepts for managing ecological systems and landscapes. We conclude that natural variability concepts provide a framework for improved un- derstanding of ecological systems and the changes occurring in these systems, as well as for evaluating the consequences of proposed management actions. Understanding the history of ecological systems (their past composition and structure, their spatial and temporal variability, and the principal processes that influenced them) helps managers set goals that are more likely to maintain and protect ecological systems and meet the social values desired for an area. Until we significantly improve our understanding of ecological systems, this knowledge of past ecosystem functioning is also one of the best means for predicting impacts to ecological systems today. These concepts can also be misused. No a priori time period or spatial extent should be used in defining natural variability. Specific goals, site-specific field data, inferences derived from data collected elsewhere, simulation models, and explicitly stated value judg- ment all must drive selection of the relevant time period and spatial extent used in defining natural variability. Natural variability concepts offer an opportunity and a challenge for ecologists to provide relevant information and to collaborate with managers to improve the management of ecological systems.
By 1883, free-roaming plains bison were nearly exterminated. Efforts to save the bison rested on the efforts of a few Canadians and Americans. By 1900, efforts were successful to save the bison from extinction and their numbers continued to increase. The largest herd in North America was located near Wainwright, Alberta. The Wainwright bison population quickly increased to >10 000. About 6000 buffalo were gradually moved to the newly-created Wood Buffalo National Park in northern Alberta. Today, there are >50 000 bison in government and privately-owned herds. -from Author
Efforts to save remnant wild bison from extermination have resulted in the establishment of herds on private, public, and tribal lands. Ironically, their successful restoration has evolved into a profitable agricultural industry and a practical alternative to raising domestic cattle. Bison restoration actively managed by humans raises ecological, ethical, and evolutionary questions about whether we are compromising their native ability to function in a grasslands ecosystem. In this essay I examine current bison management practices, conflicting human values about land-use practices, and emerging land-use initiatives focusing on wild bison and ecosystem restoration in the northern Great Plains.
Through dam building and feeding activities, beaver act as a keystone species to alter hydrology, channel geomorphology, biogeochemical pathways and community productivity. In Quebec, density of dams on the small streams (= or <4th order) studied averages 10.6 dams/km; the streams retain up to 6500 m3 of sediment per dam, and the wetted surface area of the channel is increased up to several hundredfold. Beaver are also active in larger order streams (= or >5th order), but their effects are most noticeable along riverbanks and in floodplains. Comparative carbon budgets per unit area for a riffle on 2nd order Beaver Creek and a beaver pond downstream show the pond receives only 42% of the carbon acquired by the riffle annually, but because the pond has a surface area 7 times greater than the riffle, it receives nearly twice as much carbon as the riffle per unit of channel length. Carbon in the pond has an estimated turnover time of 161 yr compared to 24 yr for the riffle. Beaver ponds are important sites for organic matter processing. -from Authors
Delineating a species' geographic range using the spatial distribution of museum specimens or even contemporary detection-non-detection data can be difficult. This is particularly true at the periphery of a species range where species' distributions are often disjunct. Wolverines (Gulo gulo) are wide-ranging mammals with discontinuous and potentially isolated populations at the periphery of their range. One potentially disjunct population occurred in the Sierra Nevada Mountains, California, USA, and appears to have been extirpated by the 1930s. Many early 20th century naturalists believed that this population was connected to other populations occurring in the Cascade Range of northern California, Oregon, and Washington, USA, but a recent analysis of historical records suggests that California wolverines were isolated from other populations in North America. We used DNA extracted from museum specimens to examine whether California wolverines were isolated. Both nuclear and mitochondrial DNA data indicate that California wolverines were genetically distinct from extant populations, suggesting long-term isolation. We identified 2 new control region (mitochondrial DNA) haplotypes located only within California. We used these data and referenced sequences from the Rocky Mountains, USA, to make inferences regarding potential wolverine translocations into California. In addition, we used these genetic data to make inferences about wolverine conservation throughout western North America.
Advocates of Traditional Ecological Knowledge (TEK) have promoted its use in scientific research, impact assessment, and ecological understanding. While several examples illustrate the utility of applying TEK in these contexts, wider application of TEK-derived information remains elusive. In part, this is due to continued inertia in favor of established scientific practices and the need to describe TEK in Western scientific terms. In part, it is also due to the difficulty of accessing TEK, which is rarely written down and must in most cases be documented as a project on its own prior to its incorporation into another scientific undertaking. This formidable practical obstacle is exacerbated by the need to use social science methods to gather biological data, so that TEK research and application becomes a multidisciplinary undertaking. By examining case studies involving bowhead whales, beluga whales, and herring, this paper describes some of the benefits of using TEK in scientific and management contexts. It also reviews some of the methods that are available to do so, including semi-directive interviews, questionnaires, facilitated workshops, and collaborative field projects.