Index of Species Information
SPECIES: Bromus japonicus
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| Japanese brome in eastern Montana. Wikimedia Commons image by Matt Lavin from Bozeman, Montana, USA - Bromus japonicus, CC BY-SA 2.0, https://commons.wikimedia.org/w/index.php?curid=68773365. |
Introductory
SPECIES: Bromus japonicus
AUTHORSHIP AND CITATION:
Howard, Janet L. 1994. Bromus japonicus. 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/graminoid/brojap/all.html [].
Revisions:
On 17 October 2018, Taxonomy section of the Species Review was revised.
Images were also added.
ABBREVIATION:
BROJAP
SYNONYMS:
None
NRCS PLANT CODE [65]:
BRJA
COMMON NAMES:
Japanese brome
Japanese chess
TAXONOMY:
The scientific name of Japanese brome is Bromus japonicus Thunb. (Poaceae)
[33,34,39,52,68,84,85,87].
Japanese brome, field brome (B. arvensis), and corn brome (B. squarrosus)
form a morphologically similar group of diploid annual grasses with
overlapping morphology [83, 86] and inconsistent taxonomy [86]. Some
systematists treat Japanese brome and field brome as synonyms [65]. However,
breeding system of Japanese brome is highly autogamous [86]. Based on
breeding system [86] and genetic studies [83, 86], this review treats Japanese
brome as a distinct species.
Japanese brome hybridizes rarely with rattlesnake brome (B. brizaeformis)
and soft brome (B. hordeaceus) [68].
LIFE FORM:
Graminoid
FEDERAL LEGAL STATUS:
No special status
OTHER STATUS:
NO-ENTRY
DISTRIBUTION AND OCCURRENCE
SPECIES: Bromus japonicus
GENERAL DISTRIBUTION:
Japanese brome is native to Eurasia. In North America it is distributed
from British Columbia east to Ontario and south to New Hampshire,
Florida, and Mexico [12,68].
ECOSYSTEMS:
FRES10 White - red - jack pine
FRES13 Loblolly - shortleaf pine
FRES14 Oak - pine
FRES15 Oak - hickory
FRES17 Elm - ash - cottonwood
FRES18 Maple - beech - birch
FRES19 Aspen - birch
FRES20 Douglas-fir
FRES21 Ponderosa pine
FRES28 Western hardwoods
FRES29 Sagebrush
FRES30 Desert shrub
FRES31 Shinnery
FRES32 Texas savanna
FRES33 Southwestern shrubsteppe
FRES34 Chaparral - mountain shrub
FRES35 Pinyon - juniper
FRES36 Mountain grasslands
FRES38 Plains grasslands
FRES39 Prairie
FRES40 Desert grasslands
FRES42 Annual grasslands
STATES:
AL AZ AR CA CO CT DE FL GA ID
IL IA IN KS KY LA MD MA MI MN
MO MT NE NV NH NJ NM NY NC ND
OH OK OR PA RI SC SD TN TX UT
VT VA WA WV WI WY DC AB BC MB
ON SK MEXICO
BLM PHYSIOGRAPHIC REGIONS:
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 PLANT ASSOCIATIONS:
NO-ENTRY
SAF COVER TYPES:
66 Ashe juniper - redberry (Pinchot) juniper
67 Mohrs (shin) oak
68 Mesquite
210 Interior Douglas-fir
220 Rocky Mountain juniper
229 Pacific Douglas-fir
233 Oregon white oak
234 Douglas-fir - tanoak - Pacific madrone
235 Cottonwood - willow
236 Bur oak
237 Interior ponderosa pine
238 Western juniper
239 Pinyon - juniper
240 Arizona cypress
241 Western live oak
242 Mesquite
243 Sierra Nevada mixed conifer
244 Pacific ponderosa pine - Douglas-fir
245 Pacific ponderosa pine
246 California black oak
249 Canyon live oak
250 Blue oak - gray pine
255 California coast live oak
SRM (RANGELAND) COVER TYPES:
101 Bluebunch wheatgrass
102 Idaho fescue
104 Antelope bitterbrush-bluebunch wheatgrass
105 Antelope bitterbrush-Idaho fescue
107 Western juniper/big sagebrush/bluebunch wheatgrass
109 Ponderosa pine shrubland
110 Ponderosa pine-grassland
201 Blue oak woodland
202 Coast live oak woodland
203 Riparian woodland
204 North coastal shrub
205 Coastal sage shrub
207 Scrub oak mixed chaparral
208 Ceanothus mixed chaparral
209 Montane shrubland
214 Coastal prairie
215 Valley grassland
301 Bluebunch wheatgrass-blue grama
302 Bluebunch wheatgrass-Sandberg bluegrass
304 Idaho fescue-bluebunch wheatgrass
309 Idaho fescue-western wheatgrass
310 Needle-and-thread-blue grama
311 Rough fescue-bluebunch wheatgrass
314 Big sagebrush-bluebunch wheatgrass
315 Big sagebrush-Idaho fescue
316 Big sagebrush-rough fescue
319 Bitterbrush-rough fescue
320 Black sagebrush-bluebunch wheatgrass
321 Black sagebrush-Idaho fescue
323 Shrubby cinquefoil-rough fescue
401 Basin big sagebrush
402 Mountain big sagebrush
403 Wyoming big sagebrush
405 Black sagebrush
406 Low sagebrush
408 Other sagebrush types
412 Juniper-pinyon woodland
503 Arizona chaparral
504 Juniper-pinyon pine woodland
509 Transition between oak-juniper woodland and mahogany-oak association
601 Bluestem prairie
602 Bluestem-prairie sandreed
603 Prairie sandreed-needlegrass
604 Bluestem-grama prairie
605 Sandsage prairie
606 Wheatgrass-bluestem-needlegrass
607 Wheatgrass-needlegrass
608 Wheatgrass-grama-needlegrass
609 Wheatgrass-grama
610 Wheatgrass
612 Sagebrush-grass
613 Fescue grassland
614 Crested wheatgrass
708 Bluestem-dropseed
709 Bluestem-grama
710 Bluestem prairie
711 Bluestem-sacahuista prairie
715 Grama-buffalograss
717 Little bluestem-Indiangrass-Texas wintergrass
720 Sand bluestem-little bluestem (dunes)
721 Sand bluestem-little bluestem (plains)
722 Sand sagebrush-mixed prairie
724 Sideoats grama-New Mexico feathergrass-winterfat
727 Mesquite-buffalograss
730 Sand shinnery oak
733 Juniper-oak
735 Sideoats grama-sumac-juniper
HABITAT TYPES AND PLANT COMMUNITIES:
In the West, Japanese brome occurs in prairie, pinyon-juniper
(Pinus-Juniperus spp.), sagebrush (Artemisia spp.) steppe, and desert
shrub-grassland communities. It is most common on disturbed sites, but
is also found in undisturbed communities [19,38,44]. It occasionally
occurs in openings in ponderosa pine (Pinus ponderosa) or other
low-elevation forest types [53]. It is uncommon in the East, where it
is reported only from disturbed areas [33,59]. Plant associates are
listed below by location and community type.
Eastern Wyoming shortgrass prairie: Wyoming big sagebrush (A.
tridentata ssp. wyomingensis), fourwing saltbush (Atriplex canescens),
Gardner's saltbush (A. gardneri), rubber rabbitbrush (Chrysothamnus
nauseosus), blue grama (Bouteloua gracilis), threadleaf sedge (Carex
filifolia), sand bluestem (Andropogon gerardii var. paucipilis), prairie
Junegrass (Koeleria macrantha), needle-and-thread grass (Stipa comata),
western wheatgrass (Pascopyrum smithii), cheatgrass (Bromus tectorum),
and plains prickly pear (Opuntia polyacantha) [23].
Southwestern South Dakota mixed-grass prairie: western wheatgrass, red
threeawn (Aristida purpurea), cheatgrass, buffalo grass (Buchloe
dactyloides), plains silver sagebrush (Artemisia cana ssp. cana),
Russian-thistle (Salsola kali), and scarlet mallow (Sphaeralcea
coccinea) [10].
Central Oklahoma tallgrass prairie: big bluestem (Andropogon gerardii
var. gerardii), little bluestem (Schizachyrium scoparium), switchgrass
(Panicum virgatum), Indiangrass (Sorghastrum nutans), black-eyed Susan
(Rudbeckia hirta), and Carolina geranium (Geranium carolinianum) [2].
North-central Texas mesquite savanna: honey mesquite (Prosopis
glandulosa var. glandulosa), buffalo grass, sideoats grama (Bouteloua
curtipendula), and Texas wintergrass (Stipa leucotricha) [37].
Mesa Verde, Colorado, pinyon-juniper woodland: annual sunflower
(Helianthus annuus), pigweed (Chenopodium pratericola), wheat (Triticum
aestivum), and mountain brome (Bromus carinatus). True pinyon (Pinus
edulis) and Utah juniper (Juniperus osteosperma) were adjacent to but
not within this fire-disturbed community [19].
Northeastern California sagebrush steppe: medusahead (Taeniatherum
caput-medusae), cheatgrass, Columbia needlegrass (Stipa columbiana),
bluebunch wheatgrass (Pseudoroegneria spicata), and bottlebrush
squirreltail (Elymus elymoides). Basin big sagebrush (Artemisia
tridentata ssp. tridentata) and low sagebrush (A. arbuscula ssp.
longicaulis) were adjacent to but not within this grazing-disturbed
community [7].
Japanese brome was ranked as important in high-disturbance willow (Salix
spp.)-zone stream channels of south-central Oklahoma [51].
MANAGEMENT CONSIDERATIONS
SPECIES: Bromus japonicus
IMPORTANCE TO LIVESTOCK AND WILDLIFE:
Livestock use Japanese brome heavily in fall and early spring [61,66].
It is an important and highly palatable fall diet item of white-tailed
deer [77], and bison also graze it heavily in fall. Plants rapidly
loose palatability as they mature [61]. Like all annuals, Japanese
brome is unpredictable forage: Yields are high in wet years but low in
dry years [61,66].
Wild turkeys eat Japanese brome seeds [46].
PALATABILITY:
Japanese brome palatability for livestock and wildlife has been rated as
follows [17]:
CO MT ND UT WY
cattle good fair fair good fair
sheep fair fair fair fair fair
horses good fair fair good fair
pronghorn ---- ---- poor fair ----
elk ---- ---- ---- fair ----
mule deer ---- ---- poor ---- ----
white-tailed deer ---- ---- poor ---- ----
small mammals ---- ---- ---- fair ----
upland game birds ---- ---- poor fair ----
waterfowl ---- ---- poor poor ----
NUTRITIONAL VALUE:
Japanese brome rapidly decreases in nutritive content and digestibility
as it matures [61]. Analysis of fresh, immature Japanese brome yielded
the following data [48]:
crude fiber 28.7%
protein (N x 6.25) 16.1%
digestible protein
cattle 11.6%
goats 11.6%
horses 11.2%
sheep 12.0%
calcium 0.40%
phosphorus 0.26%
COVER VALUE:
Japanese brome provides fair cover for small nongame birds and mammals
and poor cover for upland game birds and waterfowl [17].
VALUE FOR REHABILITATION OF DISTURBED SITES:
Japanese brome is not used for reclamation, but its seeds are often
present in salvaged topsoils. Its presence on reclamation sites can
slow succession toward desirable perennials [4,58].
OTHER USES AND VALUES:
No information is available on this topic.
OTHER MANAGEMENT CONSIDERATIONS:
Japanese brome is usually regarded as a noxious weed on rangelands and
prairies because it competes with native perennials for water and
nutrients [4,29,61,66]. It is reported in general literature as
increasing with moderate to heavy grazing [56,61,66]. It may decrease
under such grazing regimes, however. Whisenant and Uresk [74] observed
that Japanese brome density in Badlands National Park, South Dakota,
which is only lightly grazed, appeared much greater than in more heavily
utilized adjacent rangeland. They hypothesized that litter accumulation
with little or no grazing created a favorably mesic environment for
Japanese brome germination and establishment.
Mechanical treatments may increase, sometimes greatly, Japanese brome
populations. With favorable soil moisture Japanese brome establishes
wherever native vegetation is disturbed and soil nitrogen levels are
temporarily increased [30]. Mowing a Kansas tallgrass prairie in August
resulted in one such Japanese brome population increase [32].
Control: The best way to prevent or minimize Japanese brome invasion is
to minimize soil disturbance. Where Japanese brome has already
established, it can be reduced with herbicides. Atrazine is most
commonly used [13,40]. A list of other pre- and postemergent herbicides
effective against Japanese brome is available [79].
Discing or moldboard plowing followed by a second disking or herbicide
treatment after the germination period reduced Japanese brome on the
Texas Southern Great Plains [14].
BOTANICAL AND ECOLOGICAL CHARACTERISTICS
SPECIES: Bromus japonicus
GENERAL BOTANICAL CHARACTERISTICS:
Japanese brome is an introduced, cool-season, annual grass from 8 to 48
inches (20-120 cm) tall. It sheaths are hairy; the blades are glabrous
to hairy. The inflorescence is an open panicle bearing 6 to 13 caryopses
[34,36,38,43,68]. Roots may be shallow [61], or surprisingly deep for
an annual. Roots of plants in Lewistown, Montana, reached depths of 5
feet (150 cm), with most roots concentrated between 2.7 and 4.7 feet (80
and 140 cm) below ground. Japanese brome root density surpassed that of
five other annual bromes also occurring at the site [40].
RAUNKIAER LIFE FORM:
Therophyte
 |
| Japanese brome fruiting in the Wenatchee foothills of Washington. Wikimedia Commons image by Thayne Tuason. |
REGENERATION PROCESSES:
Japanese brome reproduces entirely from seeds. Plants are self-fertile
or autogamous; outcrossing is rare [86]. The seeds require a moist substrate
for germination. A heavy thatch or litter layer improves germination
rates by retaining moisture [5]. Seeds germinate over a broad
temperature range: from just above freezing to over 95 degrees
Fahrenheit (35 deg C) [5,25]. Under laboratory conditions a
majority (67%) of fresh seed was immediately germinable, but under
natural conditions most seeds are retained on the parent plant until
late fall or winter, which delays germination [5]. Some seeds are
dispersed off-site in animal hides or dung: The majority of seeds found
in bison chips on the Wichita Mountains Wildlife Refuge, Oklahoma, were
Japanese brome [11]. Other seeds fall near the parent plant [4,5].
Seeds are probably not deeply buried. In Wind Cave National Park, South
Dakota, Whisenant [71] found few Japanese brome seeds deeper than 1.2
inches (3 cm) below ground. Late fall- and winter-dispersed seeds
undergo dormancy and need a period of afterripening the following summer
before germination occurs. Most seeds therefore germinate in fall and
are from the previous year's crop [5]. Fall precipitation increases
successful germination, and above-average precipitation is critical when
the litter layer is sparse to absent [70]. Whisenant [71] reported that
Japanese brome density in Wind Cave National Park was much greater in
summers that followed heavy fall rains. Winter and spring precipitation
did not greatly affect Japanese brome density. A minority of seeds
germinate in spring; plants growing from these seeds tend to flower
later in the year, if at all [5,22,40]. Japanese brome is a prodigious
seed producer [4]. The long-term viability of Japanese brome seeds is
unknown, but seeds remain viable for at least several years. Soil from
north-central Kentucky, collected after the germination period had passed,
still contained an average concentration of 2,325 viable Japanese brome
seeds per square meter [5].
Seedlings overwinter in a rosettelike growth form [5].
SITE CHARACTERISTICS:
Japanese brome invades disturbed and undisturbed sites. It dominates
disturbed areas in the Jackson Hole Wildlife Park, Wyoming, where it
occurs on bridle paths, roadsides, gravel pits, and heavily used or
burned picnic sites [55]. In other areas it is reported from
site-prepared plantations [53], old prairie dog mounds [50], moderately
to heavily grazed rangelands [56], and undisturbed mixed-grass prairie
[72].
Japanese brome grows on soils of various textures including sand [8],
silt [9], clay [7], and claypan [35]. It usually occurs on mesic sites
[28,49,75]. Fine-textured soils with good litter cover promote best
growth [70]. It is apparently intolerant of alkaline soils [64].
SUCCESSIONAL STATUS:
Japanese brome colonizes disturbed sites [4,19]. It sometimes decreases
with succession: Four years following elimination of disturbance
(logging and ranching) on the University of Kansas Natural History
Reserve, Japanese brome had 7.4 percent cover. Twelve years later it
was present only in trace amounts. Twenty-seven years later it was
absent from the community [24]. Japanese brome may persist or even
dominate some late seres or climax communities, however [40,42].
Huschle and Hironaka [42] listed a Japanese brome phase of the bluebunch
wheatgrass-Sandberg bluegrass (Agropyron spicatum-Poa secunda
[Pseudoroegneria spicata-Poa secunda]) habitat type by the middle and
lower Snake River, Idaho.
SEASONAL DEVELOPMENT:
Japanese brome usually germinates in fall. It shows some fall
vegetative growth, winter dormancy, vigorous spring vegetative growth,
and late spring flowering. It fruits and dies in summer, and seeds
disperse from the dead plants in fall and winter [4,5,22,71].
Overwintering Japanese brome seedlings are among the first grasses to
resume growth in spring [29]. A minority of seeds germinate in spring,
and flowering occurs in late summer in these plants. Spring-germinating
plants in northern latitudes are usually killed by frost before seeds
are ripe [71,75].
Baskin and Baskin [5] reported that in north-central Kentucky,
germination occurs from early September to mid-October; flowering begins
in early May; seeds ripen and plants die from late June to early July;
and seeds disperse from late October until March.
Frequency (%) of occurrence of phenological stages in central Oklahoma
was reported as follows [2]:
germinating vegetative
seedling growth anthesis fruiting dissemination
winter 45.8 ---- 5.0 9.2 9.2
spring ---- 51.7 13.3 ---- ----
summer ---- 15.6 4.4 43.3 42.2
autumn 1.5 ---- ---- 32.3 32.3
FIRE ECOLOGY
SPECIES: Bromus japonicus
FIRE ECOLOGY OR ADAPTATIONS:
Except in wet years, fire tends to reduce Japanese brome populations
[31]. The reduction usually lasts for only 1 or 2 years, however
[31,65]. Some seed is killed by fire, but seedbank reserves,
reproductive capacity, and competitive ability of Japanese brome are
usually sufficient to allow for repopulation of an area within 2 years
unless the site is reburned [69,72,78].
Studies conducted when precipitation was below normal reported
reductions in Japanese brome populations for 2 postfire years [28,30].
Since litter accumulations are more critical for germination and
seedling establishment when precipitation is low, drastic population
reductions can be expected when burning is followed by below-average
precipitation [71].
Fire during wet years may not reduce Japanese brome populations.
Studies conducted during years of high precipitation showed no change in
Japanese brome density the summer after burning [73].
Kirsch and Kruse [44] hypothesized that the successful establishment and
spread of Japanese brome across the Northern Great Plains is a direct
result of fire suppression: The resulting thicker surface mulch created
a more mesic microenvironment for seeds and seedlings [44,72]. Japanese
brome populations will probably continue to increase in the absence of
fire [71]. In the Flint Hills of Kansas, for example, bluestem
(Andropogon gerardii and Schizachyrium scoparium) prairie grazed and
burned annually has remained in excellent condition, while prairie
grazed but not burned has been invaded by Japanese brome and Kentucky
bluegrass (Poa pratense) [3].
FIRE REGIMES:
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:
Ground residual colonizer (on-site, initial community)
Initial-offsite colonizer (off-site, initial community)
FIRE EFFECTS
SPECIES: Bromus japonicus
IMMEDIATE FIRE EFFECT ON PLANT:
Fire kills Japanese brome. Some of the seeds retained in panicles are
also killed [28,29,69,73,78].
PLANT RESPONSE TO FIRE:
Whisenant [71] suggested that Japanese brome postfire response is best
explained as a function of level of litter reduction by fire and the
amount of fall precipitation following fire. Since litter accumulations
are more critical for seed germination and seedling establishment in dry
than wet years, populations are reduced when burning is followed by
below-average precipitation. During wet years, fire has little impact
on subsequent generations.
A 1973 to 1975 South Dakota study showed that spring, summer, or fall
burning reduced Japanese brome for two postfire growing seasons. During
the study, prescribed burning was followed by 2 years of drought [28].
In another South Dakota study where prescribed fire was followed by 2
years of above average precipitation, Japanese brome densities at
postfire years 1 and 2 were similar to prefire densities [72].
Whisenant and others [73] reported that Japanese brome frequency was not
significantly changed in postfire year 1 by fires in September 1979,
January 1980, or March 1980. In eastern Montana, spring burning
reduced Japanese brome for one postfire growing season. Subsequent
years were not evaluated [76].
Prescribed fire was used on a western wheatgrass-green needlegrass
(Pascopyrum smithii-Stipa viridula) prairie in Wind Cave National Park,
South Dakota, to test Japanese brome response to fire. Treatments were
fall (Sept. 18, 1973), winter (Feb. 13, 1974), and spring (April 10,
1974) burning. Japanese brome density (stems/sq ft) on May 24, 1974,
was as follows [27]:
Treatment
| fall burn control | winter burn control | spring burn control | unburned |
| 0.8 80.0 | 33.8 57.3 | 15.7 56.1 | 56.9 |
Only one study was found describing Japanese brome postfire response in
palouse prairie. A July 1961 wildfire in a bluebunch
wheatgrass-Sandberg bluegrass stand in southeastern Washington reduced
Japanese brome and cheatgrass populations for at least 2 years.
Japanese brome percentage frequency was as follows [16]:
unburned burned
postfire yr 2 42 10
postfire yr 4 30 50
postfire yr 12 32 18
Two accounts of Japanese brome postfire response in the Southwest were
found. In Mesa Verde, Colorado, Japanese brome was a component of an
initial (postfire yrs 1 & 2) annual sunflower-pigweed community
following a July 15 to August 7, 1959, wildfire in a true pinyon-Utah
juniper (Pinus edulis-Juniperus osteosperma) woodland [19].
The spring following prescribed winter fire in a honey mesquite/Texas
wintergrass woodland in Coleman County, Texas, cool-season annuals
including Japanese brome were reduced by 74 percent. At postfire year 2
there was a trend toward more annual grasses on burned than unburned
sites [62,6].
On ponderosa pine and Douglas-fir communities in the Blue Mountains
of northeastern Oregon, Japanese brome cover and frequency in postfire year
4 were higher on thinned-and-burned sites than on thinned, prescribed burned,
or unburned control sites. Japanese brome was determined to be an indicator
species for thinned-and-burned sites (P≤0.05). For further information
on the effects of thinning and burning treatments on Japanese brome and
48 other species, see the Research Project Summary of Youngblood and
others' [82] study.
DISCUSSION AND QUALIFICATION OF PLANT RESPONSE:
For further information on Japanese brome response to fire, see Fire Case Studies.
The following Research Project Summaries provide information on prescribed
fire and postfire response of plant species including Japanese brome.
FIRE MANAGEMENT CONSIDERATIONS:
Whisenant [72] stated that fire exclusion in northern mixed-grass
prairie has improved conditions for Japanese brome establishment at the
expense of native grasses. In the absence of intensive grazing, litter
accumulations in northern mixed-grass prairie stabilize after 5 to 6
postfire years [1,18]. Whisenent [74] has recommended burning every 5
years or less to reduce litter accumulations. This reduces Japanese
brome populations, particularly when fall precipitation is low.
However, he cautions managers to balance the benefits of litter against
need to reduce Japanese brome when preparing fire management plans.
Benefits of litter include soil stabilization and insulation, moisture
retention, and promotion of perennials [80].
Gartner and others [28] recommended burning Japanese brome in the ripe
seed stage in order to maximize kill of seeds in panicles.
Whisenant [70] has developed regression equations modelling Japanese
brome density and seed production as affected by fire.
SPECIES: Bromus japonicus
FIRE CASE STUDY CITATION:
Howard, Janet L., compiler. 1994. Prescribed Fire control of Japanese brome in
Badlands National Park, South Dakota. In: Bromus japonicus. 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/ [].
REFERENCES:
Whisenant, Steven G. 1985. Effects of fire and/or atrazine on Japanese
brome and western wheatgrass. Proc. Western Soc. Weed Science. 38:
169-176. [69].
Whisenant, Steven G. 1990. Postfire population dynamics of Bromus
japonicus. American Midland Naturalist. 123: 301-308. [71].
Whisenant, S. G.; Bulsiewicz, W. R. 1986. Effects of prescribed burning
on Japanese brome population dynamics. Proceedings of the 15th
International Grassland Congress: 803-804. [72].
Whisenant, Steven G.; Uresk, Daniel W. 1990. Spring burning Japanese
brome in a western wheatgrass community. Journal of Range Management.
43(3): 205-208. [74].
SEASON/SEVERITY CLASSIFICATION:
Spring/Severity not measured
STUDY LOCATION:
The study area was in Badlands National Park in south-central South Dakota.
PREFIRE VEGETATIVE COMMUNITY:
The study was conducted in a stand of native shortgrass prairie in good
condition. Japanese brome (Bromus japonicus) and western wheatgrass
(Pascopyrum smithii) codominated the site. Green needlegrass (Stipa
viridula), sand dropseed (Sporobolus cryptandrus), threadleaf sedge
(Carex filifolia), blue grama (Bouteloua gracilis), and buffalo grass
(Buchloe dactyloides) were minor components of the community. Japanese
brome tiller density averaged 1,500 per square meter; western wheatgrass
tiller density averaged 273 per square meter.
TARGET SPECIES PHENOLOGICAL STATE:
Japanese brome seedlings were 1 to 2 inches (3-5 cm) tall when the April
fires were set, and 3 to 4 inches (8-10 cm) tall when the May fires were
set.
SITE DESCRIPTION:
The mean growing season in the Park is 126 days. Annual precipitation
is approximately 384 millimeters, 303 of which falls during the growing
season. Average temperature is 47 degrees Fahrenheit (8.3 deg C), with
temperatures rising to 100 degrees Fahrenheit (38 deg C) in summer and
dropping to -20 degrees Fahrenheit (-29 deg C) in winter. Summer and
fall relative humidity has a wide diurnal variation, ranging from 85
percent in morning to 40 percent by afternoon. Precipitation from
October 1983 to July 1984 (the first year of the study) was above
average, with of most of it occurring in fall. Precipitation from
October 1984 to July 1985 (the second year of the study) was 61 percent
of normal. Soil at the study site is Larvie silty clay (fine,
montmorillonitic, mesic, vertic Camborthid).
The study site was relatively undisturbed. It had never been cultivated
and had not been burned or grazed by domestic livestock for at least 25
years. White-tailed deer, pronghorn, bison, and Rocky Mountain bighorn
sheep reside in the Park, but grazing effects were not apparent at the
study site.
FIRE DESCRIPTION:
Fire treatments were: (1) unburned, (2) burned in April 1983, (3)
burned in May 1984, (4) burned in April 1983 and April 1984, (5) burned
in May 1983 and May 1984, (6) clipped in April 1983, (7) clipped in May
1983, (8) atrazine application in September 1983, (9) burned in April
1983 with atrazine application in September 1983, and (10) burned in
April 1984.
Environmental and fuel variables during the fires were as follows:
Ambient Wind Relative Fuel Fine
Date Burned Temperature Speed Humidity Moisture Fuels
(deg C) (km/hr) _________%________ (g/sq m)
20 April 1983 22 6-9 40 18 211
19 May 1983 14 19-23 78 38 298
16 April 1984 14 5-23 43 28 276
9 May 1984 16 13-16 56 35 272
FIRE EFFECTS ON TARGET SPECIES:
Japanese brome tiller density and standing crop were significantly
reduced the first year after the 1984 fires. Tiller density and
standing crop were not significantly reduced the second postfire year.
Burning resulted in greater reductions than did clipping, indicating
that mortality resulted from heat rather than simply foliage removal.
Atrazine applied as a preemergent herbicide significantly reduced
Japanese brome density.
In July 1984, Japanese brome density and standing crop were as follows:
Treatment Treatment Number Density Standing Crop
(tillers/sq m) (g/sq m)
___________________________________________________________________________
Control vs. 1 2,617 14.8
1983 fire 2 2,028 NS 19.9 NS
Control vs. 1 2,617 14.8
1984 fire 3,10 23** 0.7*
Control vs. 1 2,617 14.8
1983 & 1984 fires 4,5 580** 4.7*
1984 fire vs. 3,10 23 0.7
1983 & 1984 fires 4,5 580** 4.7 NS
Control vs. 1 2,617 14.8
atrazine application 8 19** 0.0*
1983 clipping vs. 6,7 3,250 24.7
1983 fire 2 2,028* 19.9 NS
1983 fire vs. 2 2,028 19.9
1984 fire 3,10 23** 0.7**
1983 fire followed by
atrazine application vs. 9 19 1.5
atrazine application 8 77 NS 0.0 NS
atrazine application vs. 8 19 0.0
1984 fire 3,10 23 NS 0.7 NS
___________________________________________________________________________
NS means contrast is not significant; * means P<0.05;
** means P<0.01
Japanese brome densities in the spring were positively correlated with
litter weight and autumn precipitation. As precipitation decreased,
litter became more important. Burning reduced seed production for at
least three growing seasons. Seed production in 1984 and 1985 was
greatest in controls and lowest in recently burned plots. In 1986, seed
production was reduced in plots burned in 1984 but not in untreated
plots or those burned in 1983.
Litter seedbanks were reduced when precipitation was below normal. The
litter seedbank was reduced drastically after the combination of drought
and fire in 1985. Reduction in the litter seedbanks on burned sites
lasted for 3 years. The soil seedbank was also reduced for 3 years, but
the reduction was less drastic.
Japanese brome seedling density and seedbank reserves, measured in July,
were as follows:
_______________________________________________________________________________
Seed production (per sq m) Control Burned April 1983 Burned April 1984
1983 73,160 a 1,620 b 67,815 a
1984 94,212 a 46,644 b 368 c
1985 1,410 a 785 b 375 c
1986 31,584 a 29,911 a 12,208 b
1987 30,416 a 27,897 a 38,157 a
Litter seedbank (per sq m)
1984 12,460 a 11,775 a 700 b
1985 187 a 112 b 18 c
1986 6,712 a 263 b 89 b
1987 7,914 a 869 b 475 b
Surface soil seedbank (per sq m)
1984 11,852 a 10,760 a 11,512 a
1985 7,859 a 6,923 ab 5,754 b
1986 4,587 a 3,712 a 2,251 b
1987 6,810 a 2,861 b 2,551 b
Seedling density (per sq m), measured in April
1983 2,738 a 2,299 a 2,516 a
1984 2,287 a 2,417 a 2,381 a
1985 578 a 554 a 72 b
1986 990 a 523 b 65 c
1987 2,114 a 1,847 a 1,710 a
______________________________________________________________________________
Means within a row followed by the same letter are not significantly
different from each other at P=0.05
FIRE MANAGEMENT IMPLICATIONS:
Fire that reduces litter accumulations reduces the next generation of
Japanese brome. Carryover of Japanese brome in the seedbank is usually
sufficient to establish subsequent generations. As water becomes more
limiting, litter becomes increasingly important in determining the size
of Japanese brome populations.
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FEIS Home Page
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