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IntroductoryAUTHORSHIP AND CITATION: Groen, Amy H. 2005. Apocynum androsaemifolium. In: Fire Effects Information System, [Online]. U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station, Fire Sciences Laboratory (Producer). Available: https://www.fs.usda.gov/database/feis/plants/forb/apoand/all.html []. FEIS ABBREVIATION: APOAND SYNONYMS: Apocynum ambigens (Greene) Apocynum pumilum (Greene) Apocynum scopulorum (Greene) NRCS PLANT CODE [182]: APAN2 COMMON NAMES: spreading dogbane dogbane flytrap dogbane TAXONOMY: The currently accepted scientific name for spreading dogbane is Apocynum androsaemifolium L. (Apocynaceae) [7,22,23,39,42,61,64,73,74,75,77,81,85, 86,87,96,98,113,127,128,137,167,190,191,200].Varieties are as follows:
A. a. var.androsaemifolium
Hybrids: Hybridization is common within the genus Apocynum [6,39]. Spreading dogbane
commonly hybridizes with Indian hemp (A. cannabinum) to produce intermediate dogbane
(Apocynum × medium Greene) [23,61,113,137,189,191]. Sources which recognize intermediate
dogbane as a separate variety include [75,87,98,167,200].
DISTRIBUTION AND OCCURRENCESPECIES: Apocynum androsaemifolium
Spreading dogbane is widely distributed throughout North America. It occurs in every U.S. state except Hawaii, Kansas, and the southeastern states of Louisiana, Mississippi, Florida, and South Carolina [182]. Spreading dogbane can be found in most Canadian provinces [74] and occurs in Mexico [137]. A. a. var. incanum can be found scattered throughout Nova Scotia [137] and A. a. var. pumilum is found in west-central Montana [98]. Intermediate dogbane is found primarily in areas where spreading dogbane and Indian hemp habitats overlap [137,189,190,191]. Plants database provides a distributional map for spreading dogbane. ECOSYSTEMS [57]: FRES10 White-red-jack pine FRES11 Spruce-fir FRES19 Aspen-birch FRES20 Douglas-fir FRES21 Ponderosa pine FRES22 Western white pine FRES23 Fir-spruce FRES26 Lodgepole pine FRES37 Mountain meadows FRES39 Prairie STATES/PROVINCES: (key to state/province abbreviations) UNITED STATES
CANADA
MEXICO
BLM PHYSIOGRAPHIC REGIONS [21]: 1 Northern Pacific Border 2 Cascade Mountains 3 Southern Pacific Border 4 Sierra Mountains 5 Columbia Plateau 6 Upper Basin and Range 7 Lower Basin and Range 8 Northern Rocky Mountains 9 Middle Rocky Mountains 10 Wyoming Basin 11 Southern Rocky Mountains 12 Colorado Plateau 13 Rocky Mountain Piedmont 14 Great Plains 15 Black Hills Uplift 16 Upper Missouri Basin and Broken Lands KUCHLER [95] PLANT ASSOCIATIONS: K002 Cedar-hemlock-Douglas-fir forest K005 Mixed conifer forest K007 Red fir forest K008 Lodgepole pine-subalpine forest K010 Ponderosa shrub forest K011 Western ponderosa forest K012 Douglas-fir forest K014 Grand fir-Douglas-fir forest K015 Western spruce-fir forest K016 Eastern ponderosa forest K017 Black Hills pine forest K018 Pine-Douglas-fir forest K019 Arizona pine forest K020 Spruce-fir-Douglas-fir forest K074 Bluestem prairie K093 Great Lakes spruce-fir forest K095 Great Lakes pine forest K096 Northeastern spruce-fir forest K097 Southeastern spruce-fir forest K102 Beech-maple forest K107 Northern hardwoods-fir forest K108 Northern hardwoods-spruce forest SAF COVER TYPES [50]: 1 Jack pine 5 Balsam fir 12 Black spruce 13 Black spruce-tamarack 15 Red pine 16 Aspen 18 Paper birch 20 White pine-northern red oak-red maple 21 Eastern white pine 22 White pine-hemlock 27 Sugar maple 28 Black cherry-maple 38 Tamarack 42 Bur oak 44 Chestnut oak 45 Pitch pine 51 White pine-chestnut oak 55 Northern red oak 63 Cottonwood 107 White spruce 108 Red maple 109 Hawthorn 201 White spruce 202 White spruce-paper birch 203 Balsam poplar 204 Black spruce 206 Engelmann spruce-subalpine fir 207 Red fir 210 Interior Douglas-fir 211 White fir 212 Western larch 213 Grand fir 215 Western white pine 217 Aspen 218 Lodgepole pine 220 Rocky Mountain juniper 224 Western hemlock 227 Western redcedar-western hemlock 228 Western redcedar 229 Pacific Douglas-fir 230 Douglas-fir-western hemlock 235 Cottonwood-willow 236 Bur oak 237 Interior ponderosa pine 243 Sierra Nevada mixed conifer 244 Pacific ponderosa pine-Douglas-fir 245 Pacific ponderosa pine 246 California black oak 247 Jeffrey pine 249 Canyon live oak 251 White spruce-aspen 252 Paper birch 253 Black spruce-white spruce 254 Black spruce-paper birch SRM (RANGELAND) COVER TYPES [150]: 101 Bluebunch wheatgrass 102 Idaho fescue 104 Antelope bitterbrush-bluebunch wheatgrass 105 Antelope bitterbrush-Idaho fescue 109 Ponderosa pine shrubland 110 Ponderosa pine-grassland 210 Bitterbrush 216 Montane meadows 302 Bluebunch wheatgrass-Sandberg bluegrass 304 Idaho fescue-bluebunch wheatgrass 314 Big sagebrush-bluebunch wheatgrass 317 Bitterbrush-bluebunch wheatgrass 319 Bitterbrush-rough fescue 411 Aspen woodland 420 Snowbrush 601 Bluestem prairie 710 Bluestem prairie 802 Missouri prairie ALASKAN RANGELANDS 920 White spruce-paper birch 921 Willow HABITAT TYPES AND PLANT COMMUNITIES: Spreading dogbane is common in dry, open areas and is often found after a disturbance. It is recognized as dominant or codominant in the Rocky Mountain Douglas-fir (Pseudotsuga menziesii var. glauca)/white spirea (Spiraea betulifolia) habitat type of central Idaho [160] and as dominant in old jack pine (Pinus banksiana) stands in the boreal forests of Saskatchewan [112]. BOTANICAL AND ECOLOGICAL CHARACTERISTICSSPECIES: Apocynum androsaemifolium
GENERAL BOTANICAL CHARACTERISTICS:
Spreading dogbane is a native perennial that can grow to 40 inches (100 cm) in height [39]. Stems are erect and diffusely branched, glabrous, and lack a central axis [73,86,98,116,191]. Leaves are opposite, spreading or drooping, glabrous above and pubescent beneath. Leaf size ranges from 0.4 to 5 inches (1-12 cm) in length and 0.2 to 2 inches (0.5-6 cm) in width [64,81,98,189,190,191]. The flowers of spreading dogbane are erect or nodding and small, 0.2 to 0.3 inch (6-8 mm) long [127,147]. The corolla is typically 0.2 to 0.5 inch (4-12 mm) long, broadly campanulate, and approximately 3 times the length of the calyx [61,64]. Spreading dogbane follicles are 1.6 to 6 inches (4-15 cm) long and pendulous or erect when mature [116,191]. Epidermal hair around the head of the stigma ensures that pollen is not lost [56]. Seeds are numerous, 2 to 3 mm long with a 0.4 to 0.8 inch (1-2 cm) long coma [60,64,70]. Spreading dogbane has rhizomes that have been detected to depths of greater than 10 inches (25 cm) and are located primarily in mineral soil [195]. Intermediate dogbane can grow to 40 inches (100 cm) in height [98]. It produces progeny with low pollen fertility [39] and can appear identical to either of the parent species, spreading dogbane or Indian hemp [6].
The inflorescence of A. a. var. pumilum is often larger and the corolla more tubular
than that of spreading dogbane
[74].
Pollination: Spreading dogbane is insect and self-pollinated [83]. Insects transfer pollen from the anther to the stigma upon withdrawal of the proboscis. Cross-pollination occurs when pollen remains adhered to the proboscis and is transferred to the stigma of another flower [56]. In Colorado, approximately 71 species of insect were recorded visiting spreading dogbane over a 15-hour period. None had detectable amounts of pollen from Apocynum spp. plants [83]. A study in South Dakota concluded that behavior of 2 bumblebee species was determined by the density of spreading dogbane plants and availability of alternative food sources [126]. Breeding system: No information is available on this topic. Seed production: Spreading dogbane produces "numerous" seeds [39,116,127]. Seed dispersal: Spreading dogbane seed is wind dispersed [4,159,161,180]. Seed banking: There is no indication that spreading dogbane stores its seed in soil [158,159,160,161]. Germination: Germination requirements for spreading dogbane are not well known [161]. Seed collected from the prairies of Wisconsin in 1946 had 56% germination rates when stratified for 2 months and 36% germination rates when not stratified. The seed was planted in flats and exposed to temperatures of 65to 70 ºF (18-21 ºC) for 2 months before being stratified outdoors or kept indoors at 40 ºF (4 ºC) for 2 to 3 months [65]. In a study to determine the viability of seeds after submersion in water with temperatures ranging from 33 to 81 ºF (0.5-27 ºC), most spreading dogbane seeds either germinated and/or deteriorated in the first 3 months of submersion. Those that remained firm had germination rates ranging from <1% to 8% following 3 to 24 months of water submersion while germination rates for seed that was not submerged ranged from 53% to 91%. None of the seeds germinated after 36 or more months of submersion [33]:
Apocynum spp. are able to germinate on newly-burned soil [171]. Seedling establishment/growth: No information is available on this topic.
Asexual regeneration:
Asexual reproduction of spreading dogbane is attained through rhizomatous sprouts
[9,161]. Sprouting from rhizomes has also been observed following disturbance
[29,165].
SUCCESSIONAL STATUS: Spreading dogbane can occur in various successional stages. It does well in full sun or partial shade [161] and is considered a representative mid-seral species in multiple habitat types [158,159,160,161]. Spreading dogbane often provides important cover in locations with sparse vegetation [199] such as recently disturbed areas [187]. In Indiana, it was identified along with other forbs and shrubs in the early stage of prairie encroachment by trees [149]. Spreading dogbane is found in early successional stages on the shores of Lake MacDonald in northwestern Montana [67] and is considered a "secondary" species in Michigan aspen (Populus spp.) associations [58].
In Manitoba, wooden screens were placed to allow 25%, 50%, 75%, and 100% shade over plots
which had been fire-pruned, burned with a propane burner resulting in ground temperatures
of 260 to 480 ºF (125-250 ºC)). Spreading dogbane sprouted in plots allowing 75% shade with
10% frequency and 6% cover and did not return to any of the other plots [76], suggesting
shade tolerance in spreading dogbane. Variability in light tolerance may exist across
populations and/or locations.
Flowering dates following 6 years of observation in southeastern North Dakota were as follows [26]:
Intermediate dogbane flowers from May to August in Arizona [87]. Fruits develop from September to October in the Carolinas [128]. A. a. var. incanum in northeastern Oregon was in bud the 3rd week of July, flowering the 4th week, flowering and fruiting the 1st and 2nd weeks of August, and fruiting the last 2 weeks of August and the 1st week of September where it occurred with vine maple (Acer circinatum) associations. Within coast Douglas-fir (Pseudotsuga menziesii var. menziesii) associations, A. a. var. incanum was in bud the 1st week of August and flowering the 2nd and 3rd week of August [133]. FIRE ECOLOGYSPECIES: Apocynum androsaemifoliumFIRE ECOLOGY OR ADAPTATIONS: Fire adaptations: Spreading dogbane recolonizes burned sites immediately after fire through rhizomes [9,29,51,163,165,166,166]. The position of perennating parts below the soil surface allows spreading dogbane to survive short (12 to 15 year) fire intervals in boreal forests [140]. Spreading dogbane may also recolonize a site through seed germination from off-site seed sources [4], although examples have not been documented. Fire regimes: Spreading dogbane is found in communities that experience long and short fire return intervals. It is most common in dry environments with short fire intervals [9], but has been found among interior ponderosa pine (Pinus ponderosa var. scopulorum) stands with historic mean fire return intervals of 20 to 23 years that had not burned in 96 years [197]. Where spreading dogbane occurs in interior ponderosa pine-Rocky Mountain Douglas-fir habitat types, grazing has resulted in the promotion of younger, denser stands of even-aged trees that are more susceptible to disease and insect outbreaks and consequent increases in high severity fire risks [202]. Where spreading dogbane is found with quaking aspen (Populus tremuloides), the longevity of stands is dependant upon the time of fire following germination. Short fire intervals discourage aspen regeneration where extensive root masses have had insufficient time to develop [58]. Although the effect of fire on spreading dogbane within these associations has not been reported, it is unlikely that variable fire return intervals would affect its presence. Spreading dogbane in white fir (Abies concolor) habitat of southern Oregon is able to withstand periods of 15 years or more without fire and was detected in areas that had not burned in 134 years [108]. The following table provides fire return intervals for plant communities and ecosystems where spreading dogbane is important. Find fire regime information for the plant communities in which this species may occur by entering the species name in the FEIS home page under "Find Fire Regimes".
POSTFIRE REGENERATION STRATEGY [165]: Rhizomatous herb, rhizome in soil Geophyte, growing points deep in soil Secondary colonizer (on-site or off-site seed sources) FIRE EFFECTSSPECIES: Apocynum androsaemifolium
IMMEDIATE FIRE EFFECT ON PLANT:
Reports indicate that spreading dogbane is able to germinate on recently burned soil [171],
likely from off-site seed sources [4]. In the absence of frequent disturbances, populations
of spreading dogbane are reported to die out [9], although populations have been reported
up to 134 years following fire [108].
California: Spreading dogbane has been observed after fires in northern California [93,169]. Following fire in the hardwood forests of northwestern California, it was reported to have 1.5% and 3.4% mean relative cover on 2 sites [169]. Idaho: Spreading dogbane cover increased from 0.5% to 0.9% following a shelterwood cut at the Priest River Experimental Forest in northern Idaho. Areas subsequently treated with a "moist" burn (duff was moist and fire was conducted 1 day during the warmest, driest period) had 1.0% cover prior to cutting and burning and 2.6% cover 1 year after treatment. Areas treated with a "dry" burn (duff was dry and burn was conducted over the course of 2 days throughout the evening, night, and morning) had 0.5% cover prior to treatment and 1.4% cover 1 year following cutting and burning [154]. Cover and frequency of spreading dogbane on high intensity prescribed burns in Idaho were significantly higher (P<0.01) than cover and frequency on control and low intensity burn sites averaged across the 1st 3 years [10]. Following a large wildfire in a western larch (Larix occidentalis)-Douglas-fir cover type in northern Idaho, spreading dogbane constituted a maximum of 10% to 14% of cover within the 1st postfire decade due to vegetative reproduction [164]. It was reported on 11 of 21 plots measuring 16 × 82 feet (5 × 25 m), returning 2 to 15 years postfire on sites that had previously supported standing timber or shrubfields. It was not reported on clearcut sites. Three plots reported flowering in the 1st year [165]. Logging and helicopter yarding were conducted in Rocky Mountain Douglas-fir habitat types of central Idaho in September through November, 1976. Micro plots on each of the logged areas were burned under prescription or by wildfire following harvest activities and vegetation plots were measured 1, 2, 5, and 10 years postburn. A comparison of burned and unburned areas in the years following fire resulted in the following cover [59]:
Maine: Five years after a wildfire on Peaks Island off the coast of Maine, spreading dogbane was considered a characteristic "shrub" layer. The area had also experienced fire 26 and 28 years prior to measurements [37]. On Mount Desert Island off the coast of Maine, spreading dogbane returned through vegetative reproduction 1 year after the 1923 wildfire and was considered "abundant" [155]. Michigan: In Michigan spreading dogbane was found on mature jack pine stands, unburned jack pine stands within a 3-year-old clear cut, and jack pine plots burned under prescription 1 and 2 years previously. The highest frequency of spreading dogbane was found on the 1-year-old prescribed burn site [1]. In the gray birch-red maple (Betula populifolia-Acer rubrum) habitat type of Painted Rocks National Lakeshore, spreading dogbane had an average frequency of 13% and constancy of 9% in an area that had previously experienced fire [102]. In northern lower Michigan, spreading dogbane populations were assessed at 5 sites supporting eastern white pine (P. strobus), red pine (P. resinosa) , northern red oak (Q. rubra), and red maple that had previously experienced natural and/or prescribed burns. Based on 100 1×1 m² quadrats at each site, spreading dogbane was absent from 4 sites and found with 1% frequency on 1 site 27 years following fire [143]. Out of 53 recorded years, it showed the greatest frequency 16, 38, 45, and 50 years following fire [144]. Spreading dogbane in mature red pine-eastern white pine stands on the southwestern lower peninsula of Michigan had highest cover (0.96%) on a site that had experienced 3 biennial burns and was not found on sites that had been burned once or were unburned. Frequencies obtained from 1 m² plots following various burn treatments are as follows [117]:
Minnesota: In a study related to burn succession in coniferous forests of Minnesota, spreading dogbane was found on 7 of 10 burns. It was abundant in the herbaceous stage after a pine burn [63]. In the boreal forests of northern Minnesota, plots were examined in order to determine the effects of fire, logging, and forest type on biodiversity. Spreading dogbane was found on 54.3% of postfire stands and 45.7% of post-logging stands. Prefire occurrence was not recorded [130]. In northeastern Minnesota, a single spreading dogbane plant was recorded immediately after fire and 4 plants were recorded the following year in a forest supporting coniferous and hardwood species. Over the next 3 years, spreading dogbane was absent from all sample sites [118]. Intact red pine soil blocks extracted from an unburned site and a site burned 3 years previous were exposed to moist greenhouse conditions for 3 months. No seed or seedlings were detected in the unburned soil. The equivalent of 109,000 spreading dogbane seedlings per hectare sprouted in greenhouse samples obtained from the burned area. No seed was found in sieved samples of burned soil, suggesting that seed had blown in from adjacent plots postfire. Spreading dogbane frequency as measured at the burn site was 0%, indicating poor establishment despite seed availability [4]. Montana: Spreading dogbane was found in Rocky Mountain lodgepole pine (P. contorta var. latifolia), Rocky Mountain Douglas-fir, spruce (Picea spp.), and subalpine fir (Abies lasiocarpa) stands 34 years following fire in Glacier National Park [68]. It was also detected following 2 wildfires and 1 broadcast burn in the northern Rocky Mountains [166]. It was reported following a shelterwood cut in interior ponderosa pine-Rocky Mountain Douglas fir forest types in Montana, on plots treated with a low-consumption burn, high-consumption burn, or no burn. Spreading dogbane responded to increased intensity of fire with increasing coverage [11]:
In a study that monitored the effects of "light" (<360ºF (180 ºC)), "medium" (360 to 570 ºF (180-300 ºC)), and "hot" (>570 ºF (300 ºC)) burn conditions in western larch-Douglas-fir habitat types, intermediate dogbane averaged 1.63% cover on light burns and 0.20% cover on hot burns 3 years following treatments [157]. New York: In south-central New York, spreading dogbane was found to be an overall increaser in 8 chestnut oak stands, 3 of which had experienced 1 fire, 3 that had experienced 2 fires, and 2 that had experienced 3 fires. Average frequency on burned sites was 39.3% while on unburned sites it was 14.3%. In a similar study conducted in 2 aspen groves, spreading dogbane had an average frequency of 47.5% on burned sites and 0% on unburned sites [171]. South Dakota: Spreading dogbane was detected after fire in the Black Hills of South Dakota. Vegetation surveys took place in July or August, 2 years following a fire that consumed all organic matter and killed all of the trees [119]. Washington: In the ponderosa pine-Douglas-fir forest types of the Entiat Experimental Forest in the Cascade mountains of Washington, 4 watersheds were "severely and uniformly burned" in 1970 and received seed, seed and fertilizer, or no treatment. Spreading dogbane was most abundant where fertilizer was applied. Refer to Tiedemann and Klock [175] for seed mix and fertilizer types used. Average cover and frequency 1 year following treatments are shown below. The average cover of spreading dogbane on all 4 watersheds 1, 2, 3, and 4 years after the fire was 0.9%, 1.4%, 1.1%, and 1.5%, respectively [176].
On a prairie site in western Washington that is burned annually as a result of military training exercises, spreading dogbane is 1 of 16 species that retains at least 0.01% cover. Mean cover and frequency are 0.2% and 16%, respectively [178,179]. In north-central Washington burns covered with dense snowbrush (Ceanothus velutinus) 20 years after fire, spreading dogbane was reported to have a "scattered" distribution [103]. Wisconsin: Spreading dogbane is considered a prevalent species on burned jack pine stands in northwestern Wisconsin with a frequency of 11.8% and is not considered prevalent in unburned stands. Nine control sites and 28 burned sites averaging 3.5 burns per stand were examined. Twenty burned stands were sampled the summer following the last spring burn while the other 8 were sampled 1 year postburn. Spreading dogbane frequency was 6.8% greater on burned sites [186]. In the bracken fern (Pteridium aquilinum) grasslands of northeastern Wisconsin, spreading dogbane is considered a "neutral" species, averaging 20.8% frequency on undisturbed sites and 17.3% frequency following burning. Thirteen sites were burned once, 2 sites were burned 3 times and 1 stand experienced 2 wildfires. Burning was done in March or April and sampling was completed in July or August of the same year or the following year. A study utilizing 6 pairs of burned and unburned stands of jack pine-northern pin oak (Q. ellipsoidalis) in north-central Wisconsin reported a 1% reduction of spreading dogbane frequency on burned sites [186]. Canada: Spreading dogbane occurred on a logged, burned site in a forest that dominated before treatment by eastern white pine and paper birch (B. papyrifera). Within 1 year of logging and 1 month of burning, spreading dogbane frequency was 5%, and aboveground biomass totaled 0.40 g in sample plots covering a total area of 5 m2 [152]. Average ground cover of spreading dogbane was less than 1% [153]. In another burn conducted with a gasoline-powered flamethrower held 4 to 12 inches (10-30 cm) above the ground surface, there was no recorded effect on spreading dogbane. Temperatures reached approximately 1700 ºF (925 ºC) [156]. Spreading dogbane in eastern Ontario was detected with 12% frequency 37 years after harvesting and burning of a site that previously supported white spruce (Picea glauca), quaking aspen, and eastern white pine [28]. Spreading dogbane has also been reported 1 year after a prescribed burn in jack pine habitat where it did not previously occur [109]. In the Engelmann spruce (P. engelmannii)-subalpine fir habitat type of the Selkirk Range in western Canada, spreading dogbane was identified soon after reforestation of a burn site [148]. Following a severe fire in spruce habitat (Picea spp.) of northern British Columbia where < 0.4 inch (1 cm) of ash and organic matter were left behind, spreading dogbane was considered one of the most common forbs. The population peaked after the 3rd year and had declined by year 5 [120]. The following Research Project Summary provides information on prescribed fire use and postfire response of many plant species, including spreading dogbane: Understory recovery after low- and high-intensity fires in northern Idaho
ponderosa pine forests In the eastern Cascades, artificial seeding following fire resulted in reduced frequency (P = 0.04) and cover (P < 0.001) of spreading dogbane populations [145]. Phenological development of spreading dogbane may be altered as a result of modifications to the thermal regime that occur postfire [52]. MANAGEMENT CONSIDERATIONSSPECIES: Apocynum androsaemifolium
Spreading dogbane is considered poisonous to domestic livestock [38,45,96,127] and is intermittently grazed by wildlife. In Idaho's Selway Game Preserve, the leaves and flowers of spreading dogbane account for 5% of elk diets from late June to early October [201]. Stomach content analysis of Rocky Mountain goats in the Crazy Mountains of Montana revealed trace amounts of spreading dogbane during the fall months[142]. Spreading dogbane provides nest-building sites for crab spiders [115], forage for forest-dwelling ground squirrels [36], and is utilized by bees for honey production [181]. Palatability/nutritional value: In central Idaho spreading dogbane has low palatability for elk and deer [159,160] and is unpalatable to black bears [158]. It is utilized by a native slug species on the dry east slopes of the Cascades, but is unpalatable to introduced European slugs [27]. Nutritional values of spreading dogbane as a percentage of total dry matter are as follows [36]:
When spreading dogbane was treated with multi-nutrient fertilizers, concentrations of B, Cu, K, N, and S were not significantly different (P>0.10) [184]:
Cover value:
Frego and Staniforth [54] maintain that spreading dogbane provides canopy cover. Species for which
this applies were not discussed.
Spreading dogbane can be successfully transplanted. Transplanting from high elevation to low elevation sites led to development that was delayed by 1 month when compared to plants currently at the low elevation site. Plants moved from low elevation to high elevation sites were advanced by 1 week in 1st bloom and peak bloom when compared to plants remaining at the low elevation site. Transplants did not produce seed at the lower sites [53]. Spreading dogbane has been used for landscaping in residence areas that seek to utilize prairie species [79].
Procedures for seed propagation of spreading dogbane can be found in [80].
In Ontario, spreading dogbane was found 6 years after the removal of vegetation from a peat bog and subsequent harvesting of up to 7 feet (2 m) of peat, but was not found in bogs that had been mined 1, 10, and 24 years previously [84]. In northern Minnesota, understory species were monitored following spring and winter full-tree logging (tree felled and taken off-site), winter tree-length logging (tree felled, limbed and only bole taken off site), and sites that received no treatment. Spreading dogbane was found on the logged sites during the 2nd season following treatment. The occurrence of spreading dogbane across treated sites was not significantly different at the P=0.05 level [121]. Spreading dogbane cover increased from 0.5% to 0.9% following a shelterwood cut at the Priest River Experimental Forest in northern Idaho [154]. In the 5 years following an 8-acre clear-cut in the northern Sierra Nevada range, the following measurements of spreading dogbane were taken [107]:
In a study to determine how light intensity correlates with frequency of spreading dogbane in red pine forests, plots exposed to variable amounts of sunlight were examined. Frequency was highest between 50% and 80% of full sunlight [151]. Spreading dogbane is not influenced by edge effects [49]. Studies conducted to determine the change in moisture content of 21 species from early summer to mid-summer indicate that spreading dogbane was 1 of 3 species to experience an increase [101]. In Idaho, biomass production of spreading dogbane in an area grazed primarily by cattle and domestic sheep was greater than 3 times that in ungrazed areas. Cover and frequency were not significantly different (P>0.05) [202]. Spreading dogbane has been successfully controlled through the use of herbicides [25,38,46,47,125,162]. Apocynum androsaemifolium: REFERENCES1. Abrams, Marc D.; Dickmann, Donald I. 1982. Early revegetation of clear-cut and burned jack pine sites in northern lower Michigan. Canadian Journal of Botany. 60: 946-954. [7238] 2. Abrams, Marc D.; Sprugel, Douglas G.; Dickmann, Donald I. 1985. Multiple successional pathways on recently disturbed jack pine sites in Michigan. Forest Ecology and Management. 10: 31-48. [7237] 3. Achuff, Peter L. 1989. Old-growth forests of the Canadian Rocky Mountain national parks. Natural Areas Journal. 9(1): 12-26. [7442] 4. Ahlgren, Clifford E. 1979. Emergent seedlings on soil from burned and unburned red pine forest. Minnesota Forestry Research Notes No. 273. St. Paul, MN: University of Minnesota, College of Forestry. 4 p. [16910] 5. Alldritt-McDowell, Judith; Coupe, Ray. 1998. The ecology of the bunchgrass zone. QP #004216. Victoria, BC: Ministry of Forests, Research Branch. 5 p. [29235] 6. Anderson, Edgar. 1936. An experimental study of hybridization in the genus Apocynum. Annals of the Missouri Botanical Garden. 23(2): 159-168. [60960] 7. Anderson, J. P. 1959. Flora of Alaska and adjacent parts of Canada. 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