Cervus canadensis (wapiti)
- Summary of Invasiveness
- Taxonomic Tree
- Notes on Taxonomy and Nomenclature
- Distribution Table
- History of Introduction and Spread
- Risk of Introduction
- Habitat List
- Biology and Ecology
- Latitude/Altitude Ranges
- Natural enemies
- Notes on Natural Enemies
- Means of Movement and Dispersal
- Pathway Causes
- Impact Summary
- Economic Impact
- Environmental Impact
- Threatened Species
- Social Impact
- Risk and Impact Factors
- Uses List
- Similarities to Other Species/Conditions
- Prevention and Control
- Links to Websites
- Distribution Maps
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PicturesTop of page
IdentityTop of page
Preferred Scientific Name
- Cervus canadensis Erxleben 1777
Preferred Common Name
International Common Names
- English: American elk; elk; Rocky Mountain elk
- Spanish: uapiti
- French: cerf wapiti
Summary of InvasivenessTop of page
Cervus canadensis is a large deer native to eastern Asia and North America. Populations of C. canadensis have been introduced into the wild in New Zealand and Italy. The New Zealand population has thrived and spread over 2000 km2 of mountainous habitat in the Fiordland region; however, this range was colonised by red deer (C. elaphus) from the 1950s and hybridization means that no pure C. canadensis are now present. A hunting organization culls red deer and obvious hybrids in this area in an attempt to keep the wapiti phenotype. C. canadensis (or their hybrids) affect the structure and composition of the forests and alpine grasslands in Fiordland, and helped cause the Endangered status of the herbivorous bird Porphyrio hochstetteri, the takahe (although the deer population in the remaining takahe range consists only of C. elaphus). The status and origin of the small Italian population are unknown. C. canadensis and their embryos or semen continue to be transported internationally for the improvement of farmed C. elaphus herds.
Taxonomic TreeTop of page
- Domain: Eukaryota
- Kingdom: Metazoa
- Phylum: Chordata
- Subphylum: Vertebrata
- Class: Mammalia
- Order: Artiodactyla
- Suborder: Ruminantia
- Family: Cervidae
- Genus: Cervus
- Species: Cervus canadensis
Notes on Taxonomy and NomenclatureTop of page
Evidence from mitochondrial DNA (Ludt et al. 2004; Skog et al. 2009) suggests the genus Cervus evolved in central Asia where several subspecies of Tarim red deer exist, perhaps as a separate species Cervus hanglu Wagner 1844 (IUCN, 2017). About seven to eight million years ago this ancestral group spread west as the various subspecies of red deer (Cervus elaphus) and east as the various subspecies of wapiti (Cervus canadensis).
This eastern ‘wapiti’ clade has taxa recognised as subspecies by IUCN (2017) in north-eastern Asia (five subspecies) and North America (three subspecies) although more divisions of the North American taxa have been used (e.g. Randi et al., 2001). The sika, Thorold’s, sambar and rusa deer of east and south Asia (C. nippon, C. albirostris, C. = Rusa unicolor, and C. = Rusa timorensis, respectively) are closely related to C. canadensis.
Red deer and wapiti have often been considered as different forms of the same species, under the name of C. elaphus, but most recent studies conclude that they are two separate valid species, as summarized in their entries in the IUCN Red List of Threatened Species (IUCN, 2017).
The main introduced population of C. canadensis in New Zealand originated from North America as C. canadensis canadensis (= C. elaphus nelsoni in Nugent (2005)) for the wild herd, or various other North American taxa such C. elaphus manitobensis, roosevelti and nelsoni as more recent introduction of sires for farmed deer (Moore and Littlejohn, 1989; Nugent, 2005). To some extent the taxonomy of the genus Cervus in parts of both the introduced range and the native range is being swamped by genetic pollution as subspecies and species (red deer, wapiti and sika) are mixed with the local deer.
Wapiti are called elk or Rocky Mountain elk in North America, which is confusing because ‘elk’ is the common name in Europe for Alces alces, known as moose in North America.
DescriptionTop of page
C. canadensis is the largest species in the genus Cervus. Adult males in Fiordland, New Zealand, in the 1960s (before substantial hybridization with red deer) weighed 260 kg on average (Smith, 1974) while adult females measured in the early 1970s weighed on average 83 kg (Nugent, 2005). Antlers, which are grown by males each year, have 12 or more points in mature bulls and often lack the bez tine in wild New Zealand bulls (Nugent, 2005). Wild New Zealand C. canadensis are about 65 -75% lighter than their North American ancestors (Nugent, 2005).
DistributionTop of page
The native range of C. canadensis extends from central Asia, south to Bhutan and east to south-east Russia in a series of patchy populations, across the Bering Strait and from southern Canada to the borders of Mexico, with a population stronghold in the Rocky Mountains. C. canadensis were extirpated from the eastern states of the USA by the beginning of the 20th century (O’Gara and Dundas, 2002) but have been reintroduced to many states in recent decades (O’Gara and Dundas, 2002; Anderson et al., 2005). Feasibility studies to reintroduce the species to additional eastern states are being conducted; it is likely that these and natural spread of the earlier reintroductions will allow much of the former range that is still suitable habitat to be reoccupied.
Introduced populations of C. canadensis occur in New Zealand (now all hybrids with red deer, C. elaphus, but retaining much of the phenotype of C. canadensis – Fiordland Wapiti Foundation, 2017) and in one small area of northwest Italy. C. canadensis (including semen and embryos) are widely imported to countries outside their natural range where red deer are farmed or ranched to increase the body size of the farmed stock (Moore and Littlejohn, 1989).
Distribution TableTop of page
The distribution in this summary table is based on all the information available. When several references are cited, they may give conflicting information on the status. Further details may be available for individual references in the Distribution Table Details section which can be selected by going to Generate Report.
|Continent/Country/Region||Distribution||Last Reported||Origin||First Reported||Invasive||Reference||Notes|
|Bhutan||Present||Native||Not invasive||IUCN, 2017||As C. canadensis wallichii|
|China||Localised||Native||Not invasive||IUCN, 2017|
|-Gansu||Present||Native||Not invasive||IUCN, 2017||As C. canadensis macneilli|
|-Qinghai||Present||Native||Not invasive||IUCN, 2017||As C. canadensis macneilli|
|-Shaanxi||Present||Native||Not invasive||IUCN, 2017||As C. canadensis macneilli|
|-Sichuan||Present||Native||Not invasive||IUCN, 2017||As C. canadensis macneilli|
|-Tibet||Present||Native||Not invasive||IUCN, 2017||As C. canadensis macneilli|
|-Xinjiang||Present||Native||Not invasive||IUCN, 2017||As C. canadensis sibiricus|
|Kazakhstan||Present||Native||Not invasive||IUCN, 2017||As C. canadensis sibiricus|
|Mongolia||Present||Native||Not invasive||IUCN, 2017||As C. canadensis sibiricus|
|-Alberta||Localised||Native||Not invasive||Canadian Wildlife Federation, 2017||About 20,000 present|
|-British Columbia||Widespread||Native||Not invasive||Canadian Wildlife Federation, 2017||About 40,000 present, some on Vancouver Island|
|-Manitoba||Localised||Native||Not invasive||Canadian Wildlife Federation, 2017||About 7,000 present|
|-Ontario||Present||Not invasive||O’Gara and Dundas, 2002||Reintroduced 1998-2001|
|-Saskatchewan||Localised||Native||Not invasive||Canadian Wildlife Federation, 2017|
|Mexico||Absent, formerly present||Native||Carrera and Ballard, 2003; Long, 2003; IUCN, 2017|
|USA||Localised||Native||Not invasive||O’Gara and Dundas, 2002||Originally present over most of USA but now extinct in eastern states. Reintroductions ongoing in many eastern states.|
|-Alaska||Localised||Introduced||Not invasive||Long, 2003||Introduced to islands|
|-Arizona||Widespread||Native||Not invasive||O’Gara and Dundas, 2002||Population of 30 000|
|-Arkansas||Localised||Not invasive||Rocky Mountain Elk Foundation, 2016||Reintroduced|
|-California||Localised||Native||Not invasive||O’Gara and Dundas, 2002||Tule subspecies|
|-Colorado||Widespread||Native||Not invasive||O’Gara and Dundas, 2002|
|-Idaho||Widespread||Native||Not invasive||O’Gara and Dundas, 2002||Population of 107 000|
|-Kansas||Localised||Native||O’Gara and Dundas, 2002|
|-Kentucky||Localised||Not invasive||O’Gara and Dundas, 2002||Reintroduced in 1997|
|-Michigan||Localised||Not invasive||Larkin et al., 2001|
|-Minnesota||Localised||Not invasive||Rocky Mountain Elk Foundation, 2016|
|-Missouri||Localised||Not invasive||Rocky Mountain Elk Foundation, 2016||Reintroduced|
|-Montana||Widespread||Native||Not invasive||O’Gara and Dundas, 2002|
|-Nebraska||Localised||Native||Not invasive||O’Gara and Dundas, 2002||Population of 150 000|
|-Nevada||Localised||Native||Not invasive||O’Gara and Dundas, 2002||Population of 17 500|
|-New Mexico||Localised||Native||Not invasive||O’Gara and Dundas, 2002||Population of 70 000|
|-North Dakota||Localised||Native||Not invasive||O’Gara and Dundas, 2002|
|-Oklahoma||Localised||Native||Not invasive||O’Gara and Dundas, 2002|
|-Oregon||Widespread||Native||Not invasive||O’Gara and Dundas, 2002||Roosevelt subspecies|
|-Pennsylvania||Localised||Not invasive||Larkin et al., 2001||Reintroduced|
|-South Dakota||Localised||Native||Not invasive||O’Gara and Dundas, 2002|
|-Tennessee||Localised||Not invasive||Rocky Mountain Elk Foundation, 2016||Reintroduced|
|-Texas||Present only in captivity/cultivation||Larkin et al., 2001||On game ranches|
|-Utah||Widespread||Native||Not invasive||O’Gara and Dundas, 2002||Population of 68 000|
|-Virginia||Localised||Not invasive||Rocky Mountain Elk Foundation, 2016||Reintroduced|
|-Washington||Widespread||Native||Not invasive||O’Gara and Dundas, 2002||Roosevelt subspecies|
|-West Virginia||Localised||Not invasive||Rocky Mountain Elk Foundation, 2016||Reintroduced|
|-Wisconsin||Localised||Not invasive||Anderson et al., 2005||Reintroduced 1995|
|-Wyoming||Widespread||Native||Not invasive||O’Gara and Dundas, 2002|
|Italy||Localised||Introduced||IUCN, 2017||La Mandria reserve, near Torino|
|-Eastern Siberia||Present||Native||Not invasive||IUCN, 2017|
|-Russian Far East||Present||Native||Not invasive||IUCN, 2017|
|New Zealand||Localised||Introduced||1905||Miers, 1966||As C. canadensis nelsoni. South island. Many also farmed|
History of Introduction and SpreadTop of page
New Zealand: C. canadensis were imported from captive herds in Washington DC and Massachusetts which apparently originated from Wyoming (Miers, 1966) in 1905. Eighteen animals were liberated in Fiordland National Park and spread at a rate of 0.64 km/year (Caughley, 1963) to cover about 2000 km2 of mountainous (up to 1800 m altitude), wet (7000 mm rainfall/year) temperate rainforest and alpine grasslands. Red deer (C. elaphus) were liberated further south in Fiordland and were colonising the area already occupied by C. canadensis from not long after C. canadensis had become established. Hybridisation has meant that no ‘pure’ C. canadensis genotypes are now present, although selective culling has meant the C. canadensis phenotype has been maintained to date (Fiordland Wapiti Foundation, 2017). Wapiti, or red deer with wapiti genetics, have escaped from farms and joined wild red deer populations in other parts of New Zealand (C. Speedy, Fiordland Wapiti Foundation, New Zealand, personal communication, 2018)
Italy: A small population of C. canadensis was introduced to the La Mandria reserve near Turin, in the northwest of the country (IUCN, 2017) but their current status is not known.
Mexico: Since 1941, several attempts have been made to introduce C. canadensis from the USA to Coahuila, northern Mexico, to replace the extinct southern subspecies C. canadensis merriami, but most failed to establish (Long, 2003).Carrera and Ballard (2003) dispute the past presence of C. canadensis merriami in Mexico.
USA: C. canadensis from the contiguous states of the USA have been released on several Alaskan islands since 1926, but appear to have established only on Afnogak Island and Etolin Island (Long, 2003).
IntroductionsTop of page
|Introduced to||Introduced from||Year||Reason||Introduced by||Established in wild through||References||Notes|
|Natural reproduction||Continuous restocking|
|New Zealand||USA||1905||Hunting, angling, sport or racing (pathway cause)||Yes||No||Miers (1966); Caughley (1963)||From Wyoming via game ranches in Washington DC and Massachusetts.|
|USA||USA||No||No||Introduced from west of the Mississippi to many eastern states where they had died out|
Risk of IntroductionTop of page
In many places where C. elaphus are farmed or ranched outside their native range, C. canadensis bulls or their semen or embryos are introduced to increase the size of offspring from the red deer hinds, allowing higher stocking rates of the smaller C. elaphus hinds but larger offspring for venison production (Moore and Littlejohn, 1989). Wapiti, or red deer with wapiti genetics, can then escape and join wild red deer populations, as has for example happened in many places in New Zealand (C. Speedy, Fiordland Wapiti Foundation, New Zealand, personal communication, 2018). Even when no animals are imported, the introduction of genetic material and subsequent escape of offspring is introducing C. canadensis genes (and occasionally phenotypes) into wild populations of Cervus in countries such as Argentina.
HabitatTop of page
In its native range, C. canadensis lives in open deciduous woodland, boreal forests, mountainous areas and upland moors, grasslands, pastures and meadows. It is generally found in hilly or mountainous regions (IUCN, 2017)
In New Zealand, the wild population lives in indigenous forest and alpine grassland in Fiordland National Park in South Island. The forests are wet (up to 7 m of rainfall per year), and temperate with winter snow. They are dominated by southern beech (Nothofagus spp.), podocarps such as rimu (Dacrydium cupressinum) and a variety of hardwoods. The alpine grasslands above 900 m altitude are dominated by snow tussocks (Chionochloa spp.). The terrain is mountainous, and steep-sided from past glaciations; it extends from fiords in the west up to about 2000 m altitude towards the east.
Habitat ListTop of page
|Terrestrial ‑ Natural / Semi-natural||Natural forests||Present, no further details||Harmful (pest or invasive)|
|Natural forests||Present, no further details||Natural|
|Natural grasslands||Present, no further details||Harmful (pest or invasive)|
|Natural grasslands||Present, no further details||Natural|
Biology and EcologyTop of page
In New Zealand, hybridisation between C. elaphus and C. canadensis in Fiordland began about 70 years ago, as C. elaphus began to invade the C. canadensis range. Early evidence of hybridisation in the wild was provided by morphometric studies on the skulls of deer shot within the area (Caughley, 1971) and later confirmed by genetic studies (Randi et al., 2001). A random sample of 156 young deer shot in the area in 2015 showed that all were now to some extent hybrids (Fiordland Wapiti Foundation, 2017).
In New Zealand, the rutting season is between mid-March and the end of April, with calves born from late November to mid-December. This is a displacement of 6 months compared to the northern hemisphere ancestors of these deer, a transition that took place within two years of the establishment of a wild population (Logan and Harris, 1967).The females have single calves (rarely twins). The age at which females first breed depends on the physical condition of the population – they breed as yearlings when conditions are good and as 3-year-olds when they are poor (Smith, 1974).
The natural lifespan of C. canadensis is about 17-18 years (IUCN, 2017).
Population size and density
In North America, the population of C. canadensis in the late 1990s was estimated at about one million. Typical population densities range from 2 to 10 individuals per km² (density can reach about 25 per km², higher figures in the literature almost certainly refer to fed populations) (IUCN, 2017). See IUCN (2017) for population figures in other parts of the native range.
The C. canadensis herd in Fiordland, New Zealand, increased after its spread into the wild in 1905 in a typical irruptive fluctuation (Caughley, 1970; Forsyth and Caley, 2006), reaching peak densities in around 1930. The expected decline and stabilisation of the population predicted by these models was confounded by official culling which began in the 1930s, more intensive recreational hunting from the 1950s, commercial exploitation from the 1960s, and current culling of C. elaphus and non-typical C. canadensis phenotypes. The density of deer (red and hybrids) within the C. canadensis range was about 2 animals/km2 in 1989 (Nugent and Sweetapple, 1989).
C. canadensis are highly adaptable and both graze grasses and browse herbs and woody plants (Poole, 1951).
ClimateTop of page
|Cf - Warm temperate climate, wet all year||Preferred||Warm average temp. > 10°C, Cold average temp. > 0°C, wet all year|
|D - Continental/Microthermal climate||Preferred||Continental/Microthermal climate (Average temp. of coldest month < 0°C, mean warmest month > 10°C)|
Latitude/Altitude RangesTop of page
|Latitude North (°N)||Latitude South (°S)||Altitude Lower (m)||Altitude Upper (m)|
Natural enemiesTop of page
|Natural enemy||Type||Life stages||Specificity||References||Biological control in||Biological control on|
|Canis lupus||Predator||All Stages||not specific|
Notes on Natural EnemiesTop of page
C. canadensis in North America suffer predation from large predators such as wolves (Canis lupus) and bears (Ursidae), where they are present. Reintroduction of wolves into Yellowstone National Park in 1995/96 reduced wapiti densities and changed the behaviour of the deer, allowing deer-preferred plants such as aspens to increase (Fortin et al., 2005).
New Zealand C. canadensis have no natural predators other than humans. The wild animals in New Zealand are generally healthy with few ectoparasites (the louse Damalinia longicornis was found once) but share several endoparasites with C. elaphus. One significant endoparasite is the nematode Elaphostrongylus cervi, which was first found in deer in Fiordland and since then has been found in farmed animals throughout New Zealand (Nugent, 2005). The wild herd in Fiordland has not been exposed to bovine tuberculosis.
Means of Movement and DispersalTop of page
Introduction of C. canadensis to new countries has been intentional; some were released in New Zealand by the tourism department (Miers, 1966). More recently, importation of semen and embryos to improved farmed deer stock (Moore and Littlejohn, 1989), and escapes from farms, have spread C. canadensis genes.
Natural dispersal rates of 0.64 km/year were estimated as the Fiordland herd in New Zealand colonised their range (Caughley, 1963).
Pathway CausesTop of page
Impact SummaryTop of page
Economic ImpactTop of page
Introduced C. canadensis and hybrids in New Zealand have no adverse economic impacts as they live entirely in uninhabited natural ecosystems. For the positive impact, see the Uses section.
Environmental ImpactTop of page
The impact of C. canadensis and hybrids on the natural ecosystems in New Zealand is the same as those for all cervids in the country. New Zealand’s ecosystems evolved in the absence of mammalian herbivores so the arrival of species such as C. canadensis has resulted in changes in structure and composition of the vegetation communities in which they exist. They remove the most palatable plant species to which they have access (understorey plants in forests and all species in grasslands), which may or may not be replaced by unpalatable species (Rose and Platt, 1987; Stewart et al., 1987). These changes may or may not be reversible if C. canadensis numbers are controlled (Coomes et al., 2003) as the state of the system is changed. The consequences may be obvious and immediate (Nugent, 2005) or subtle and long-term, as the composition of regenerating plants in the understorey changes and the mortality and replacement of the original canopy trees is influenced (Nugent et al., 2001; Forsyth et al., 2015). The effects of C. canadensis, C. elaphus and hybrids on the vegetation are one of the causes of the Endangered status of the takahe, Porphyrio hochstetteri, although (C. Speedy, Fiordland Wapiti Foundation, New Zealand, personal communication, 2018) the small current deer population in the remaining takahe range consists only of C. elaphus.
Threatened SpeciesTop of page
|Threatened Species||Conservation Status||Where Threatened||Mechanism||References||Notes|
|Phacelia insularis var. insularis (island phacelia)||NatureServe NatureServe; USA ESA listing as endangered species USA ESA listing as endangered species||California||Ecosystem change / habitat alteration||US Fish and Wildlife Service, 2008|
Social ImpactTop of page
Introduced C. canadensis and hybrids in New Zealand cause some social conflicts because they occur within a National Park, where all introduced mammals are categorised as pests to be eradicated if possible, yet they are highly valued by recreational hunters. A compromise has been reached to allow partial management by the hunters (Fiordland Wapiti Foundation, 2017).
Risk and Impact FactorsTop of page Invasiveness
- Proved invasive outside its native range
- Has a broad native range
- Abundant in its native range
- Highly adaptable to different environments
- Is a habitat generalist
- Capable of securing and ingesting a wide range of food
- Highly mobile locally
- Ecosystem change/ habitat alteration
- Modification of successional patterns
- Reduced native biodiversity
- Threat to/ loss of endangered species
- Threat to/ loss of native species
- Competition - monopolizing resources
- Interaction with other invasive species
- Highly likely to be transported internationally deliberately
- Difficult/costly to control
UsesTop of page
C. canadensis are used for recreational hunting and in deer farming, in both cases providing a source of venison (Nugent, 2005) and sometimes velvet (Gilbey and Petrezgonzalez, 2012), as well as income (in New Zealand, for example, hunters of introduced wapiti spend an estimated $1million per year in and around the township of Te Anau, which is significant economic activity in this small tourist town -- C. Speedy, Fiordland Wapiti Foundation, New Zealand, personal communication, 2018). The red deer farming and ranching industry around the world uses C. canadensis as either live animals, live embryos or semen to increase the size of red deer offspring or the size of antlers (Moore and Littlejohn, 1989).
Uses ListTop of page
- Sport (hunting, shooting, fishing, racing)
Human food and beverage
- Meat/fat/offal/blood/bone (whole, cut, fresh, frozen, canned, cured, processed or smoked)
- Source of medicine/pharmaceutical
Similarities to Other Species/ConditionsTop of page
The genus Cervus forms a ring of sub-species and species around the Northern Hemisphere. Deer at the western end of this ring (red deer, C. elaphus) have a wide phenotypic variation in body size and antler conformation, but are generally distinguished from the eastern and North American species (wapiti, C. canadensis) and southern species (sika, C. nippon) of the ring by differences in pelage and antler form. Generally, there is an increase in body size and lighter pelage across the genus from west to east. Wapiti are typically the largest species in the genus. Both sexes have a lighter coloured body and larger cream-coloured rump patch (but with dark head, neck and legs) than red and sika deer. Wapiti calves are brown with a dark dorsal strip and may have a pattern of indistinct light spots for the first few months – red deer fawns also have white spots with a distinct double row along their back that are more distinct than those in wapiti. There are differences in antler conformation between the three species, with wapiti sur-royals (the top tines in adults) sweeping backward, while those in red deer stay in the same plane as the lower tines, as do those for sika deer. Sika deer (Cervus nippon) retain the juveniles’ distinct white spots as adults, especially in their summer pelage. See King (2005) for more detailed descriptions of the three species.
Prevention and ControlTop of page
In New Zealand, the Fiordland herd is managed by a cooperative programme between the New Zealand Department of Conservation (who manage the National Park) and the Fiordland Wapiti Foundation (a non-government organisation of those with an interest in recreational hunting). The aim is to keep the total number of deer in the area to levels at which sensitive plants can persist and to maintain the high proportion of C. canadensis phenotypes in the otherwise hybrid population. In the area of Fiordland where the proportion of C. canadensis alleles in animals is highest, all red deer (C. elaphus) are shot and significant numbers of young (<3 years) and older (>9 years) females culled, but all young males that are clearly hybrids are left until they grow old enough to show clear phenotypic characters. Outside this area, all C. elaphus, most obvious hybrids, older C. canadensis-type males with poor antlers and many females are culled to help manage herd size and structure and to help maintain C. canadensis phenotypes. Most of the hunting is done by shooting from helicopters. Between 900 and 1200 deer are culled per year, suggesting a total deer population of about 4000. The recreational hunting season is during the ‘bugle’ when 400 or more hunters gain access to trophy C. canadensis in hunting blocks allocated under a ballot system (Nugent, 2005; C. Speedy, Fiordland Wapiti Foundation, New Zealand, personal communication, 2018).
In the past C. canadensis were culled as pests, exploited for venison recovery and captured alive for the New Zealand deer farming industry (Nugent, 2005).
ReferencesTop of page
Adam CL, 1994. Feeding. In: Alexander TL, Buxton D, eds. Management and Diseases of Deer: A Handbook for the Veterinary Surgeon. Penicuik, UK: Veterinary Deer Society, 44-54.
Anderson DP, Turner MG, Forester JD, Zhu J, Boyce MS, Beyer H, Stowell L, 2005. Scale-dependent summer resource selection by reintroduced elk in Wisconsin, USA. Journal of Wildlife Management, 69(1):298-310.
Berg DK, Asher GW, 2004. New Reproductive Technologies for Red Deer and Wapiti. Proceedings 21 of Deer Branch NZVA, World Deer Vet Congress held at Queenstown, New Zealand, February 2004, 71–75.
Blaxter, K. B., Kay, R. N. B., Sharman, G. A. M., Cunningham, J. M. M., Eadie, J., Hamilton, W. J., 1988. Farming the red deer. The final report of an investigation by the Rowett Research Institute and the Hill Farming Research Organisation., 169 pp..
Bringans M, 2004. Collection of semen from cervids. Proceedings 21 of Deer Branch NZVA, World Deer Vet Congress held at Queenstown, New Zealand, February 2004, 80–83.
Canadian Wildlife Federation, 2017. Hinterland who’s who.. Kanata, Ontario, Canada, Canadian Wildlife Federation, http://www.hww.ca/ Kanata, Ontario, Canada: Canadian Wildlife Federation
Carrera R, Ballard WB, 2003. Elk distribution in Mexico: a critical review. Wildlife Society Bulletin, 31:1272-1276.
Caughley G, 1963. Dispersal rates of several ungulates introduced into New Zealand. Nature, 200:280-281.
Caughley G, 1970. Eruption of ungulate populations, with emphasis on Himalayan thar in New Zealand. Ecology, 51:53-72.
Caughley G, 1971. An investigation of hybridization between free-ranging wapiti and red deer in New Zealand. New Zealand Journal of Science, 14:993-1008.
Fiordland Wapiti Foundation, 2017. Fiordland Wapiti Foundation.. Te Anau, New Zealand, Fiordland Wapiti Foundation, http://www.fwf.net.nz Te Anau, New Zealand: Fiordland Wapiti Foundation
Forsyth DM, Caley P, 2006. Testing the irruptive paradigm of large-herbivore dynamics, 87297-303.
Forsyth DM, Wilson DJ, Easdale TA, Kunstler G, Canham CD, Ruscoe WA, Wright EF, Murphy L, Gormley AM, Gaxiola A, Coomes DA, 2015. Century-scale effects of invasive deer and rodents on the dynamics of forests growing on soils of contrasting fertility. Ecological Monographs, 85(2):157-180. http://www.esajournals.org/doi/full/10.1890/14-0389.1
Fortin, D., Beyer, H. L., Boyce, M. S., Smith, D. W., Duchesne, T., Mao, J. S., 2005. Wolves influence elk movements: behavior shapes a trophic cascade in Yellowstone National Park., 86(5), 1320-1330. http://www.esajournals.org/perlserv/?request=get-document&doi=10.1890%2F04-0953 doi: 10.1890/04-0953
Gilbey, A., Perezgonzalez, J. D., 2012. Health benefits of deer and elk velvet antler supplements: a systematic review of randomised controlled studies., 125(1367), 80-86. http://journal.nzma.org.nz/journal/125-1367/5476/
Haigh JC, Hudson RJ, 1993. Farming Wapiti and Red Deer. Toronto, Canada: Mosby.
IUCN, 2017. The IUCN Red List of Threatened Species.. http://www.iucnredlist.org/
King CM, 2005. The handbook of New Zealand mammals. Melbourne, Australia: Oxford University Press. 610 pp.
Larkin JL, Grimes RA, Cornicelli L, Cox JJ, Maehr DS, 2001. Returning elk to Appalachia: foiling Murphy’s Law. In: Maehr DS, Nos RS, Larkin JL eds. Large mammal restoration. Washington, DC, USA: Island Press, 101-117
Logan PC, Harris LH, 1967. Introduction and establishment of red deer in New Zealand. Wellington, New Zealand, New Zealand Forest Service, 36 pp. (New Zealand Forest Service Information Series 55)
Ludt CJ, Schroeder W, Rottmann O, Kuehn P, 2004. Mitochondrial DNA phylogeography of red deer (Cervus elaphus). Molecular Phylogenetics and Evolution, 31:1064-1083.
Miers KH, 1966. Origins of genus Cervus and relationship of wapiti and red deer. In: Banwell BD, ed. Wapiti in New Zealand. Wellington, New Zealand: AW Reed.
Nugent G, 2005. Wapiti. In: The handbook of New Zealand mammals [ed. by King, C. M.]. Melbourne, Australia: Oxford University Press, 420-428.
Nugent G, Fraser W, Sweetapple P, 2001. Top down or bottom up? Comparing the impacts of introduced arboreal possums and 'terrestrial' ruminants on native forests in New Zealand. Biological Conservation, 99(1):65-79.
O'Gara WB, Dundas RG, 2002. Distribution: past and present. In: North American elk: ecology and management [ed. by Towell, D. E. \Thomas, J. W.]. Washington, DC, USA: Smithsonian Institution Press, 67-119.
Putman R, 1988. The Natural History of Deer. Bromley, UK: Christopher Helm.
Randi E, Mucci N, Claro-Hergueta F, Bonnet A, Douzery EJP, 2001. A mitochondrial DNA control region phylogeny of the Cervinae: speciation in Cervus and implications for conservation. Animal Conservation, 4:1-11.
Rocky Mountain Elk Foundation, 2016. Rocky Mountain Elk Foundation.. Missoula, Montana, USA, Rocky Mountain Elk Foundation, http://www.rmef.org/ Missoula, Montana, USA: Rocky Mountain Elk Foundation
Schafer EH, 1968. Hunting parks and animal enclosures in ancient China. Journal of the Economic and Social History of the Orient, 11:318-343.
Skog A, Zachos FE, Rueness EK, Feulner PGD, Mysterud A, Langvatn R, Lorenzini R, Hmwe SS, Lehoczky I, Hartl GB, Stenseth NC, Jakobsen KS, 2009. Phylogeography of red deer (Cervus elaphus) in Europe. Journal of Biogeography, 36:66-77.
Smith MCT, 1974. Biology and management of the wapiti (Cervus elaphus nelsoni) of Fiordland, New Zealand. Wellington, New Zealand, New Zealand Deerstalkers Association, 253 pp.
Suttie JM, Haines SR, Li C, 2004. Proceedings of Second Antler Science and Product Technology Symposium, Queenstown, New Zealand. New Zealand: AgResearch.
Thorleifson I, Pearse T, Friedel B, 1997. Elk Farming Handbook. Canada: Alberta Venison Council.
Wilson PR, 1984. (Editor), Annual Proceedings of Deer Branch New Zealand Veterinary Association.
Wilson PR, 2004. (Editor), Proceedings 21 of Deer Branch NZVA, World Deer Vet Congress held at Queenstown, New Zealand, February 2004.
Woodbury MR, 2004. The Basics of Chronic Wasting Disease. In Proceedings 21 of Deer Branch NZVA, World Deer Vet Congress held at Queenstown, New Zealand, February 2004, 50–53.
Yerex D, 2001. Deer, the New Zealand Story. Christchurch, New Zealand: Canterbury University Press.
OrganizationsTop of page
New Zealand: Department of Conservation, Whare Kaupapa Atawhai / Conservation House, PO Box 10420, Wellington 6143, www.doc.govt.nz
New Zealand: Landcare Research, Gerald St, Lincoln, www.landcareresearch.co.nz
ContributorsTop of page
19/12/16 Original text for Invasive Species Compendium sections by:
John Parkes, Landcare Research/Kurahaupo Consulting, New Zealand
Distribution MapsTop of page
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