• GENERAL BOTANICAL CHARACTERISTICS
• RAUNKIAER LIFE FORM
• REGENERATION PROCESSES
• SITE CHARACTERISTICS
• SUCCESSIONAL STATUS
• SEASONAL DEVELOPMENT

GENERAL BOTANICAL CHARACTERISTICS:

Antelope bitterbrush is a native, deciduous shrub [30]. The fruit is an achene, 0.13 to 0.5 inch (3-13 mm) long. Antelope bitterbrush has two common ecotypes, both present throughout its range: multiple-stemmed, decumbent plants, and single-stemmed, columnar plants [30,44,169,191]. Plants may reach 12 to15 feet (3.6-4.5 m) in height, but usually grow to 3 or 4 feet (0.9-1.2 m) [20]. The decumbent form is more prevalent at higher elevations. Antelope bitterbrush is long lived. Nord [176] reported a 115-year-old plant that was 10 inches (25 cm) high and spread over 7 square feet (1.8 m2). At a lower elevation, Nord found a 128-year-old plant that was 12 feet (3.6 m) high and 20 feet (6 m) across.

Antelope bitterbrush has a long taproot or taproots [19, 58] that reach up to 15 to 18 feet (4.5-5.4 m) in length [158,176], and few shallow roots [12].

Antelope bitterbrush sometimes has nitrogen-fixing root nodules, a result of a symbiotic association with Frankia spp. actinomycetes [2,46,151,169,192,195,238]. Degree of nodulation depends on site conditions including soil moisture content and salinity, presence of inoculants, and available nitrogen [171,192,193]. Presence of nodules, even in high numbers, does not necessarily indicate that significant amounts of nitrogen are being added to the soil [130,131,195]. Trappe [132] claims antelope bitterbrush has vesicular-arbuscular mycorrhizae, not nodule-forming actinorrhizae.

RAUNKIAER LIFE FORM:

Phanerophyte

REGENERATION PROCESSES:

Regeneration is by seed, stem layering, and sprouting [20,30,169,205]. Sprouting ability of antelope bitterbrush varies. Reports of sprouting in the literature mostly relate to fire and are discussed in "PLANT RESPONSE TO FIRE" below.

Antelope bitterbrush reaches seed-bearing age in 8 to 10 years, depending on local site conditions [105]. Flowers are pollinated by insects [21,30,] except where plants are crowded and wind pollination is possible [182]. Antelope bitterbrush is highly self-incompatible [30].

Achenes fall beneath parent plants when mature and dry [105]. The papery cover prevents seed germination until the cover rots away, which usually occurs over winter [85]. Seeds are dormant and require cool-moist stratification or damage to the seedcoat by mechanical scarification, chemical treatment, or soaking in aerated water for 1 to 2 weeks to break dormancy [33,84,163,250,246]. Four to six weeks of chilling at 36 degrees Fahrenheit (2 degrees C) is sufficient to germinate antelope bitterbrush seeds [163,248]. Seeds may enter a second dormancy if chilling requirements are not met [162,163,246,251]. Stevens and Jorgensen [212] found that 74% of antelope bitterbrush germinated after 25 years of storage. There is no available information regarding antelope bitterbrush persistence in seedbanks. Natural seedling establishment occurs only in years with normal to above-normal spring precipitation [84,133]. Artificial seeding processes that do not bury the seed are rarely successful because conditions needed for germination do not usually exist for long on the soil surface.

Rodent caches are often crucial to natural regeneration of antelope bitterbrush [55,83,85,126,199,201,204,229,236,248]. Rodents and ants may stash the entire crop of seed. Accumulation of litter and duff in forested antelope bitterbrush habitats discourages rodent caching and therefore decreases seedling regeneration [85]. Rodents return in spring to eat the sprouting cotyledons, which are a rich source of carotene. Uneaten seeds are a key source of new plants [85,169]. Rodent and insect herbivory are significant causes of establishment failure, however [85,161]. Clements and Young [55] found rodents preferred antelope bitterbrush cotyledons to millet (Panicum millaceum) seed, which is usually a preferred food. Rodent herbivory reduced ability of antelope bitterbrush seedlings to reach true leaf stage by 47 to 87% in test plots.
Ferguson and Medin [94] estimate that on an undisturbed Idaho range site dominated by antelope bitterbrush, only two antelope bitterbrush plants established per year due to competition from cheatgrass. They suggest, however, that antelope bitterbrush is likely to persist if it completes its first growing season without competition [123].

Decumbent antelope bitterbrush may layer. Layering is more prevalent above 7,000 feet (2,100 m) in California, where more than 30% of bitterbrush plants were found to layer. Only 12% did so below 7,000 feet. Layering is more common on fine-textured than coarse-textured soils [176].

SITE CHARACTERISTICS:

Antelope bitterbrush is found on all slopes and aspects, usually on well-drained, permeable soils, from 3,100 to 10,000 feet (900-3,000 m) elevation. Average annual precipitation varies from 12 to 36 inches (300-910 mm) and usually falls as winter snow [205]. In Montana west of the Continental Divide, the antelope bitterbrush-bluebunch wheatgrass association occurs from 3,500 to 5,500 feet (1,000-1,650 m) elevation, generally on southern and eastern slopes. Annual precipitation ranges from 10 to 15 inches (250-380 mm) [109,205]. In Utah, antelope bitterbrush is common on dry rolling hills with northern exposures. In the basin big sagebrush cover type, antelope bitterbrush is found on deep, permeable soils below 7,000 feet (2,100 m) elevation [179].

Antelope bitterbrush survives on rocky and arid sites due to its long taproot or taproots [19, 58] and nitrogen-fixing capacity [12,192,205]. In Idaho, Murray [170] found more plants established on lava outcroppings than in swales with deeper soils. Antelope bitterbrush occurs on substrates with minimal root restriction. It is common on coarse-textured soils and on finer-textured soils with high stone content [77]. Antelope bitterbrush is found on slightly acid soils in California [175] but on basic soils in Utah [186]. It does not tolerate saline soils [176]. Seedlings have high tolerance for extremely high surface soil temperatures [91]. In eastern Oregon and western Nevada, antelope bitterbrush is important on upland sites. It is most frequent on highly calcareous, fine-textured sedimentary soils but also occurs on loamy sand and silty loam soils [7]. In Craters of the Moon National Monument, antelope bitterbrush dominates on old cinder cones, lava flows, and other substrates of volcanic origin [14].

SUCCESSIONAL STATUS:

Antelope bitterbrush is shade intolerant [14,154,159,208]. It is an early colonizer on disturbed sites [14,192], perhaps aided by its nitrogen-fixing capacity. In areas where antelope bitterbrush dominates and natural regeneration is not occurring, old, decadent antelope bitterbrush may be the climax community [218]. Biomass productivity in antelope bitterbrush declines after 70 years [14]. Stands without disturbance become senescent and decadent [56].

Antelope bitterbrush is generally replaced by western juniper where their ranges overlap [43]. In Colorado, antelope bitterbrush is much more prevalent in seral rather than climax Colorado pinyon-Utah juniper (Pinus edulis-Juniperus osteosperma) communities [81].

Hayward [115] identified antelope bitterbrush as a xerosere species in mountain shrublands.

Leopold [150] claims antelope bitterbrush is a seral species that would be replaced by bunchgrasses in eastern California if overgrazing by livestock and wildlife had not disrupted the natural succession.

SEASONAL DEVELOPMENT:

Antelope bitterbrush flowers from early spring [21] to July. Fruits ripen from July to September, depending on elevation [30]. Old plants tend to put more energy into seed production than twig/canopy production unless stimulated by browsing [94].

Seasonal development in Wenatchee, Washington, is as follows [157]:

Growth stage                                   Date
spring dormancy                                March 3-7
full leaf on old twigs                         May 8-12
full flower                                    May 22-26
Rapid twig growth and early seed formation     June 20-24
Seed maturity                                  July 11-15
Cessation of growth                            September 2-7
leaf fall                                      November 14-18

• FIRE ECOLOGY OR ADAPTATIONS
• POSTFIRE REGENERATION STRATEGY

FIRE ECOLOGY OR ADAPTATIONS:

Antelope bitterbrush is highly susceptible to fire kill [187]. Some ecotypes sprout following fire, either from dormant buds encircling an aboveground root crown, from calluses of meristematic tissue beneath the bark, or from dormant buds on a belowground lignotuber [75,78]. Very young and very old plants (younger than 5 or older than 40-60 years) do not sprout well [29,154].

Antelope bitterbrush occurs in plant communities with a variety of fire regimes. Pre-settlement fires in the ponderosa pine/antelope bitterbrush habitat type were probably less frequent than in other ponderosa pine types due to lower fuel loading [35,60,68]. Driver and Winston [78] estimate a mean fire interval of 7 to 10 years in a ponderosa pine/bitterbrush/pinegrass habitat in north-central Washington. In a pinyon woodland in the San Bernardino Mountains of California, antelope bitterbrush sprouted and became an early dominant following several wildfires. According to the authors, the fire regime in this pinyon-juniper woodland is predominantly long-interval canopy fires, and vegetation recovers slowly after fire [233]. Fuel loading in sagebrush-bitterbrush and juniper/bitterbrush communities tends to be light except in decadent stands, where extremely dry and windy conditions may result in severe fire [191]. Of four shrub communities east of the Cascade Range in Oregon and California-antelope bitterbrush, big sagebrush, snowbrush ceanothus, and greenleaf manzanita-fuel load was lowest in antelope bitterbrush [155]. The range of fire intervals reported for some species that dominate communities where antelope bitterbrush occurs are listed below. To learn more about the fire regimes in those communities, refer to the FEIS summary for that species, under "FIRE ECOLOGY OR ADAPTATIONS."

Community dominant              Fire interval range 
                                (yrs)
interior ponderosa pine         2-42
   Pinus ponderosa var. scopulorum
Mexican pinyon                  20-70
   Pinus cembroides
Rocky Mountain Douglas-fir      40-140
   Pseudotsuga menziesii var. glauca
curlleaf mountain-mahogany      13-1350
   Cercocarpus ledifolius
Rocky Mountain lodgepole pine   25-300+
   Pinus contorta var. latifolia

POSTFIRE REGENERATION STRATEGY:

Tall shrub, adventitious bud/root crown
Small shrub, adventitious bud/root crown
Initial off-site colonizer (off-site, initial community)

• IMMEDIATE FIRE EFFECT ON PLANT
• DISCUSSION AND QUALIFICATION OF FIRE EFFECT
• PLANT RESPONSE TO FIRE
• DISCUSSION AND QUALIFICATION OF PLANT RESPONSE
• FIRE MANAGEMENT CONSIDERATIONS

IMMEDIATE FIRE EFFECT ON PLANT:

Antelope bitterbrush is very susceptible to fire kill. It is considered a weak sprouter and is often killed by summer or fall fire [27,35,51,52,173,176]. Antelope bitterbrush in some areas may sprout after light-severity spring fire [1,29,35,44,20]. Scholten [201] reports 70 and 91% of plants killed, respectively, in two separate Idaho wildfires, with 26% sprouting after the first fire and only 2% after the second fire.

DISCUSSION AND QUALIFICATION OF FIRE EFFECT:

No entry

PLANT RESPONSE TO FIRE:

Reports conflict on antelope bitterbrush's ability to sprout in response to fire [13,14,28,36,37,50,53,60,111,118,125,139,169,200,208,227,242]. Geographic and ecotypic variation is considerable. Sprouting is common in eastern Idaho, occasional in Utah, and rare in Oregon, California, and Nevada [244]. In an eastern Idaho study, 50% of burned plants and 72% of top-clipped plants sprouted. However, 33 and 21%, respectively, of those sprouts died within a few years, so sprouting may not result in good long-term survivorship rates [29]. Postfire mortality is higher in central and southeastern Idaho than in southwestern Idaho and Nevada [184]. Britton and Wright [38] claim antelope bitterbrush above 7,500 feet (2,250 m) elevation is resistant to fire due to low fuels loads.

Sprouting ability is affected by fire severity and season; plant genetics, carbohydrate stores, and age; competition; soil moisture and type; and air temperature [51,154,191]. Decumbent plants seem to sprout better [14,35,37,44,52] than columnar forms [18,96]. Columnar forms sprout either from the root crown and/or from aboveground calluses of meristematic tissue, whereas decumbent forms sprout from the root crown and from points where branches layer [44]. Columnar types sprout best when fire severity is low and postfire soil moisture is high [19].

In Idaho and Montana, Bunting and others [44] found decumbent antelope bitterbrush sprouted more frequently than columnar forms. Sprouting frequencies on spring- and fall-burned sites averaged 55 and 42%, respectively. Greatest sprouting potential was found in plants in mountain shrub and conifer (Douglas-fir or ponderosa pine) communities (60% for shrub and 49% for conifer, respectively), where plants were mostly decumbent. Decumbent antelope bitterbrush also dominated mountain big sagebrush communities, but sprouting was lower in that group, possibly due to more xeric conditions. Predominantly columnar antelope bitterbrush in basin big sagebrush and juniper (western or Utah) communities sprouted the least. Seedling success paralleled sprouting success, except that average density of antelope bitterbrush seedlings in the conifer type was much higher than average density of antelope bitterbrush sprouts. Lowest seedling density was found in the juniper communities, possibly due to seed predation by rodents.

Season of burning and environmental conditions impact antelope bitterbrush ability to survive fire and sprout. Driscoll [75] measured postfire sprouting ability of antelope bitterbrush in several Oregon burns. Sprouting success ranged from 1 to 80%. Sprouting success was less after a July fire than after a September fire. In Nevada, an August burn defoliated plants, but due to high moisture content of stemwood, plant crowns did not burn. At the same site in October, a repeat fire consumed stemwood up to 0.25 inch (0.6 cm) in diameter and all plants were killed [187,190]. Murray [170] found that postfire yields of antelope bitterbrush were less after a spring fire than a fall fire, and speculated that sprouting after a spring fire would be greater than after summer fire. When soils are moist at the time of the burn, the root crown incurs less damage. Additionally, sprouting is more likely if fires are followed by rain [36,176,242]. Clark and others [52] found mortality was higher on watered fall-burned plots than on spring-burned plots.

More plants sprouted following a light August burn than a light July burn in southern Idaho, which the authors attributed to greater carbohydrate storage in the roots in August. Most moderately and heavily burned plants were killed [225].

High fuel consumption increases antelope bitterbrush mortality and therefore favors seedling establishment [36,44]. A low intensity, high frequency fire regime favors sprouting, whereas higher intensity, less frequent fires favors seedling regeneration [78]. Driver [77], who found high sprouting rates on his study plots in Washington, suggests that successfully sprouting columnar ecotypes may have been selected on habitats with high fire frequencies. According to Agee [1], nonsprouting antelope bitterbrush is now widespread in ponderosa pine ecosystems due to fire exclusion.

Soil texture affects the thermal transfer properties of soil and therefore the ability of antelope bitterbrush to sprout from undamaged underground buds [177]. Fire is more damaging to antelope bitterbrush on fine-textured calcareous soils than on coarse-textured, well-drained soils [37]. In several Oregon burns, Driscoll [75] found plants on northerly slopes with loose, coarse-textured, nonstony soils without pumice sprout best. Plants on fine-textured, stony soil sprouted poorly.

Cheatgrass invasion has increased the amount of fine fuels in big sagebrush-antelope bitterbrush grasslands, and antelope bitterbrush is not adapted to the more frequent, high severity fires resulting from increased fuel loads. Cheatgrass may outcompete antelope bitterbrush after fire [227]. Murray [170] found prescribed burned plots in Idaho had less than half the average yields of antelope bitterbrush compared to unburned plots. He concludes that vigorous competition from grasses may have decreased seedling establishment of antelope bitterbrush.

Antelope bitterbrush seeds germinate and grow on mineral soil exposed by fire [35,108]. In the Black Hills of South Dakota, antelope bitterbrush survival was measured 10 years after planting on a burned site and in an unburned, open stand of ponderosa pine [74]. Establishment from seed and containerized seedlings was higher on burned plots:

Percent survival on:     Seeded      Planted from containerized seedlings
Burned                   22.0        20.0
Unburned                  8.3        11.0

DISCUSSION AND QUALIFICATION OF PLANT RESPONSE:

No entry

FIRE MANAGEMENT CONSIDERATIONS:

In ponderosa pine/antelope bitterbrush communities, antelope bitterbrush is more prevalent in communities where fire has been suppressed for decades than in communities that have occasionally burned [191]. However, when fire is completely excluded from ponderosa pine for a long time, antelope bitterbrush becomes decadent [10,144]. Its density declines because dying plants are not replaced [43,44,200]. Frequent Indian-set fires probably favored grasses over antelope bitterbrush on most sites. On dry or stony sites, however, fires would not have carried as well, and antelope bitterbrush probably dominated such sites [8]. According to Driver and Winston [78], frequent, low-intensity wildfire in ponderosa pine communities of north-central Washington encouraged sprouting and maintained antelope bitterbrush as a community dominant.

Following prescribed burns to restore pre-settlement condition of ponderosa pine at Lick Creek in western Montana, antelope bitterbrush mortality was 25% during the harvest phase of treatment and increased to 40% after the prescribed burning that followed. Plants surviving the treatments had greater live biomass and palatability than unburned plants [9]. Also in western Montana, burn treatments in a ponderosa pine community resulted in antelope bitterbrush mortality of 72%. Following spring fire, only two antelope bitterbrush seedlings were found on study plots. Browsing was heavy on these sites and may have reduced available seeds. Twelve percent of burned plants sprouted the first year after fire. Annual growth rate of antelope bitterbrush was greater on burned plots compared to unburned plots for the first 2 years after fire [18].

Blaisdell [28] found some antelope bitterbrush sprouting following prescribed burns in Idaho, but total production of antelope bitterbrush was far below prefire levels. Sprouting bitterbrush dominated big sagebrush 9 years after fire, since it outgrew big sagebrush regeneration from seed. Twelve years after the burn, antelope bitterbrush production was still lower on burned plots compared to unburned plots.

In western juniper-antelope bitterbrush associations, antelope bitterbrush appears more vigorous where fire has killed junipers [44,191]. Antelope bitterbrush has a low (6%) sprouting success rate, low seedling establishment, and short lifespan in western juniper communities [42]. In these communities, regular but not too frequent fires are required to clear out older, decadent antelope bitterbrush and western juniper; to establish new antelope bitterbrush seedlings; and/or to encourage sprouting [42,108].

In dry Douglas-fir habitat types, antelope bitterbrush requires fire to reduce competition from conifer seedlings [35]. Prescribed fire in mesic forest communities maintains a subclimax community type and therefore encourages antelope bitterbrush establishment [44].

Antelope bitterbrush recovery from fire often takes too long for fire to be a useful tool in managing antelope bitterbrush [15,49,170,181]. Gruell [108] claims a fire frequency of 5 to 20 years would result in sparse distribution and low density of antelope bitterbrush. Driver and Winston [78] found fire recovery in the Craters of the Moon National Monument to take 15 to 20 years. Barrington and others [14] claim antelope bitterbrush density remains lower than prefire density for over 30 years in ponderosa pine communities on the eastern slope of the Cascade Range in Washington. Wright [242] reported that antelope bitterbrush was not fully recovered 27 years after a fire in a ponderosa pine community on the Warm Springs Reservation, Oregon. In contrast, Davis and others [68] found that antelope bitterbrush established quickly in a burned ponderosa pine/antelope bitterbrush habitat type on the Lolo National Forest, Montana.

Rodent-cached seeds are an important source of antelope bitterbrush regeneration after fire [44,225]. Rodent caches near or in a burned area may suffer less from seed predation following a fire because of reduced cover for rodents [56].

In British Columbia, Demarchi and Lofts [73] evaluated the nutritional content of antelope bitterbrush following fire. They concluded that there was a 3-year increase in nitrogen; a 2-year increase in calcium; a 1-year increase in phosphorus, potassium, and zinc; a decrease in copper; and no change in manganese.

• CASE NAME
• SEASON/SEVERITY CLASSIFICATION
• STUDY LOCATION
• PREFIRE VEGETATIVE COMMUNITY
• TARGET SPECIES PHENOLOGICAL STATE
• SITE DESCRIPTION
• FIRE DESCRIPTION
• FIRE EFFECTS ON TARGET SPECIES
• FIRE MANAGEMENT IMPLICATIONS

CASE NAME:

Effects of prescribed fire on antelope bitterbrush in Wyoming

REFERENCE:

Cook, J. G.; Hershey, T. J.; Irwin, L. L. 1994 [58]

SEASON/SEVERITY CLASSIFICATION:

One fire took place in June, one in September, and one in April.

STUDY LOCATION:

Three prescribed burned sites within 30 km of Encampment, in south-central Wyoming.

PREFIRE VEGETATIVE COMMUNITY:

The sites were dominated by antelope bitterbrush (Purshia tridentata), mountain big sagebrush (Artemisia tridentata ssp. vaseyana), and Saskatoon serviceberry (Amelanchier alnifolia). Common graminoids included bluebunch wheatgrass (Pseudoroegneria spicata), spike fescue (Leucopoa kingii), needle-and-thread grass (Hesperostipa comata), and Ross sedge (Carex rossii). Areas surrounding the study sites support quaking aspen (Populus tremuloides) and lodgepole pine (Pinus contorta) communities.

TARGET SPECIES PHENOLOGICAL STATE:

No entry

SITE DESCRIPTION:

Climate is semi-arid. The authors describe the study sites as high elevation and mesic, which is not typical antelope bitterbrush habitat. The region's average precipitation is 38 cm; average temperature is 5§ C. At approximately 2,400 meters, the study sites were slightly higher in elevation than regional climate stations, so they are probably wetter and cooler than these averages. Study sites are in steep canyons with lithic soils of igneous and metamorphic bedrock. The sites have east aspects. Mule deer and Rocky Mountain bighorn sheep use the area often; elk and pronghorn use it occasionally.

FIRE DESCRIPTION:

There is no specific information available about the fires themselves, but the following table outlines some environmental conditions on the study sites at the time of the fires.

               Date     Temp.(oC)   Rel. Hum. (%)  Wind (km/h)
Douglas Cr.    6/85     26          24             16-20
Encamp. NE     9/85     17          33             13-20
Prospect Mt.   4/87     11          17             5- 7

FIRE EFFECTS ON TARGET SPECIES:

The following table describes survival (% of prefire density +/- 95% confidence intervals) of antelope bitterbrush after prescribed burning from 1986 to 1989. All antelope bitterbrush plants at the Douglas Creek study site died after burning.

               Postfire year 1    Postfire year 2    Postfire year 3
Douglas Cr.    0                  0                  0
Encamp.  NE    47 +/- 10          35 +/-  9          34 +/-  9
Prospect Mt.   66 +/- 12          56 +/- 12          56 +/- 12

FIRE MANAGEMENT IMPLICATIONS:

The Douglas Creek burn that killed all of the antelope bitterbrush on site was a summer burn with the highest temperature and the greatest wind speeds of the three prescribed burns. Relative humidity was low. The habitat type investigated in this study is higher and more mesic than typical antelope bitterbrush habitats. Therefore, conclusions drawn in this study may not be universally applicable. However, findings of this study concur with much of the literature. Summer burning is most likely to kill antelope bitterbrush outright. Spring burning, when carbohydrate stores in the roots are highest, is most appropriate to encourage survival and sprouting of antelope bitterbrush.

While postfire density of antelope bitterbrush varied from 34 to 56% of prefire levels, increases in twig production increased biomass after fire, so postfire and prefire biomass were roughly equal. Fire may be a useful tool to enhance ungulate habitat by reducing standing dead matter, opening the canopy for grass production, and stimulating antelope bitterbrush twig growth.

Purshia tridentata: References

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Related categories for SPECIES: Purshia tridentata | Antelope Bitterbrush