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Vegetation biomass dynamics and patterns of sexual reproduction in a northern mixed-grass prairie.


The indigenous flora of the Great Plains region of North America evolved under widely fluctuating climatic conditions and chronic herbivory (Coupland, 1958; Dix, 1962; Wells, 1970; Milchunas et al., 1988; Lauenroth et al., 1994). Currently, florae in this region are evolving with the additional influence of recently ([less than]100 years) introduced alien species. One of the most ubiquitous introduced species is Bromus japonicus,(2) a cool-season, annual grass, that has successfully invaded large portions of grazed as well as ungrazed North American Great Plains, mixed-grass prairie (e.g., see Whisenant, 1990; Haferkamp et al., 1993; Heitschmidt et al., 1987, 1995).

We know from general observation that Bromus japonicus can modify the physiognomy of mixed-grass prairie communities. We know also that the invasion of Bromus tectorum, another introduced cool-season, annual grass, has resulted in a successional conversion of many western North America sagebrush-perennial bunchgrass-dominated communities to B. tectorum-dominated communities (Mack, 1981; Mack and Pyke, 1984). However, we are uncertain as to the potential of B. japonicus to be a keystone species in altering the rate, direction and extent of ecological succession in the North American mixed-grass prairie region. Such knowledge is critical if we intend to manage these grasslands for long-term sustainability. Thus, our objective in this study was to characterize potential plant propagation processes by quantifying vegetation growth dynamics and sexual reproduction patterns of a northern mixed grass prairie community containing an abundance of B. japonicus.


The study site was the Fort Keogh Livestock and Range Research Laboratory located near Miles City, Montana (105[degrees]50[minutes]W, 46[degrees]20[minutes]N). Regional topography ranges from rolling hills to broken badlands with small intersecting streams flowing intermittently into large permanent rivers located in broad, nearly level valleys. Indigenous vegetation on the 22,500-ha station is a Bouteloua-Stipa-Agropyron mixed-grass dominant (Kuchler, 1964). Long-term annual precipitation averages 338 mm with about 60% received from April through August [ILLUSTRATION FOR FIGURE 1 OMITTED]. Daily temperatures occasionally exceed 37 C during summer whereas winter temperatures occasionally dip below -40 C. The average frost-free period is 150 d.

The 3-ha study area was located within a 30-ha livestock grazing exclosure established in 1985. The indigenous plant community was dominated by Bouteloua gracilis, a warm-season, perennial grass, and Pascopyrum smithii, a cool-season, perennial grass. Other important species were Bromus japonicus, a cool-season, annual grass; Poa secunda, a cool-season, perennial grass; Sporobolus cryptandrus, a warm-season, perennial grass; Festuca octoflora, a cool-season, annual grass; Plantago patagonica, a cool-season, annual forb; and Opuntia polyacantha, a warm-season, succulent. Soils were fine, montmorillonitic Borollic Camborthids of the Kobar series. A-horizon soil texture graded from silty loam to silty clay loam. Slope was [less than]3%.


Three 0.025 ha (10 by 25 m) sample sites were selected for study from within the 3 ha study area. Site selection was based on a visual assessment of the communities' emulation of a "typical" Northern Great Plains indigenous plant community. Each site consisted of 20 proximate, 10-m long transects alternating between a width of 1 m (sample area) and 1.5 m (sample collection access area). Each 1-m wide sample belt was subdivided into ten 1-[m.sup.2] plots that were then subdivided into sixteen 625 [cm.sup.2] (25 by 25 cm) sample plots. Thirteen of these plots were randomly selected for sampling on each sample date using a centrally placed 100 [cm.sup.2] circular ring quadrat. We harvested herbage and seed standing crops on 10 dates between September 1991 and August 1993 and counted seedlings on 21 dates.

Aboveground standing crops were estimated by species by clipping at soil surface and weighing after drying at 60 C for 48 h. Seedling densities were estimated by counting before harvest. Number of seeds was estimated by species in the laboratory after drying. Because we could not discriminate between Bromus japonicus and B. tectorum seedlings, and because our standing crop data showed B. japonicus was the overwhelming dominant Bromus species, we considered all Bromus seedlings as B. japonicus.


Aboveground standing crops. - Seven species of perennial grasses, 1 species of sedge, 4 species of annual grasses, 14 species of forbs, and 3 species of shrubs and succulents contributed to standing crop estimates (Table 1). Total standing crop ranged from about 110 g [m.sup.-2] in late winter to about 380 g [m.sup.-2] in midsummer. Perennial grasses dominated standing crop [ILLUSTRATION FOR FIGURE 2 OMITTED] with the two dominant species being Bouteloua gracilis and Pascopyrum smithii with a combined standing crop of about 210 g [m.sup.-2] in late spring, 1992 and also in midsummer, 1993. The contribution of B. gracilis and P. smithii to total standing crop ranged from 48% in the spring of 1992 to 79% in late fall, 1992, whereas their contribution to perennial grass standing crop ranged between 84 and 95% in the same interval.

Standing crop of annual grasses ranged from a high of about 41 g [m.sup.-2] in late spring 1992 to 3 g [m.sup.-2] in August 1993 [ILLUSTRATION FOR FIGURE 2 OMITTED] and was dominated by Bromus japonicus (Table 1). Except during summer 1993 when B. japonicus standing crop was near zero, its contribution to total standing crop was relatively constant across dates ranging from 8 to 14%. Standing crop of other annual grasses never exceeded 4 g [m.sup.-2] on any sample date whereas standing crop of forbs never exceeded 8 g [m.sup.-2] except during summer, 1993. Shrub/succulent standing crop was dominated by Opuntia polyacantha (Table 1) with only a scattering of Ceratoides lanata and Coryphantha missouriensis.

Seed production. - Four species of annual grasses, 7 species of perennial grasses, 6 species of forbs and Opuntia polyacantha yielded harvestable seed (Table 1). Temporal patterns of seed production, retention and dissemination were similar among species groups [ILLUSTRATION FOR FIGURE 3 OMITTED], although absolute seed densities differed. Seed densities peaked in late spring and were dominated by the annual grasses (12,435 [m.sup.-2]) with the dominant species being Bromus japonicus (10,430 [m.sup.-2]). Except during summer 1993 when both aboveground standing crop and seed density of B. japonicus were low, its contribution to total seed production ranged from 18% (670 [m.sup.-2]) in early winter 1992, to 68% (4530 [m.sup.-2]) in midsummer 1992. Thus, its relative contribution to total seed production was much greater than its 8 to 13%

contribution to standing crop. The only other annual grass displaying prolific seed production [TABULAR DATA FOR TABLE 1 OMITTED] capacity was Festuca octoflora with a peak density of 1865 seeds [m.sup.-2] in late spring 1992 (Table 1).

Peak seed density for the perennial grasses was 4020 seeds [m.sup.-2] [ILLUSTRATION FOR FIGURE 3 OMITTED]. Major contributors were Poa secunda (3900 seeds [m.sup.-2]) and Sporobolus cryptandrus (2340 seeds [m.sup.-2]) (Table 1). On a relative basis, the two dominant standing crop species, Bouteloua gracilis and Pascopyrum smithii, contributed considerably less to seed than herbage production as their seed densities never exceeded 120 and 25 seeds [m.sup.-2], respectively.

Maximum aerial seed density of forbs was 1290 seeds [m.sup.-2] [ILLUSTRATION FOR FIGURE 3 OMITTED]. Dominant species were Plantago patagonica (880 seeds [m.sup.-2]), Hedeoma hispidum (250 seeds [m.sup.-2]) and Draba reptans (160 seeds [m.sup.-2]) (Table 1). Seed densities of several species of forbs were presumably underestimated since their periods of seed rain were very short (i.e., [less than]30 d). Opuntia polyacantha was the only shrub/succulent species for which seed densities were estimated with a peak of 295 seeds [m.sup.-2] in July 1992.

Seedling densities. - Five species of perennial grasses, four species of annual grasses and 12 species of forbs contributed to seedling populations (Table 1). Annual grasses were the dominate species [ILLUSTRATION FOR FIGURE 4 OMITTED] with Bromus japonicus seedling density peaking at 2080 seedlings [m.sup.-2] in late September 1991. Festuca octoflora was a subdominant species with seedling density peaking at 1090 seedlings [m.sup.-2] in spring 1992. Dominant forb species were Plantago patagonica, Hedeoma hispidum, Draba reptans and Androsace occidentalis. Seedling densities of perennial grasses were substantially less than for the annual grasses and forbs. The dominant perennial grass seedlings were Poa secunda with 60 seedlings [m.sup.-2] in April 1993. Seedling densities of biennial and perennial forbs were negligible during the study with a cumulative density for Taraxacum officinale, Tragopogon dubius, and Astragalus sp. of [less than]30 seedlings [m.sup.-2].

Temporal patterns of seedling emergence were dominated by annual planta [ILLUSTRATION FOR FIGURE 4 OMITTED]. Patterns of emergence for annual grasses and forbs were similar between September 1991 and July 1992 although Bromus japonicus seedlings emerged about 1 wk earlier than other annual grasses and forbs in 1991. A flush in rates of germination and seedling establishment occurred in late September 1991 following above-normal rainfall [ILLUSTRATION FOR FIGURE 1 OMITTED]. Seedling densities in late September were 3100 annual grass seedlings [m.sup.-2] and 1200 annual forb seedlings [m.sup.-2].

Annual plant seedling densities declined greatly between late September 1991 and late February 1992 [ILLUSTRATION FOR FIGURE 4 OMITTED]. This decline was presumably the result of two factors: (1) cold winter temperatures; and (2) herbivory by larvae of Grammia blakei, a moth in the Arctiidae family (identified by D.C. Ferguson, Research Entomologist, United States Department of Agriculture-Agricultural Research Service, Beltsville, Maryland). An apparent second wave of annual grass seedlings was observed between late February and late March 1992. However, close examination revealed only a minor portion of this pulse was from newly emergent seedlings; rather most of the pulse was attributable to regrowth of previously defoliated annual grass plants, particularly Bromus japonicus plants. Surprisingly, only a few other annual grasses regrew and no regrowth of annual forb seedlings was observed. The rapid decline in seedling densities from March to April 1992 was caused by maturation of annual seedlings and their concomitant removal from the seedling classification. Seedling densities of perennial grasses during the fall and winter of 1991-1992 did not exceed 30 seedlings [m.sup.-2]. Small populations of Poa secunda (51 [m.sup.-2]) and Bouteloua gracilis (10 [m.sup.-2]) seedlings were observed in March 1992.

From midspring to midsummer 1992, rates of emergence of both annual and perennial species was quite limited [ILLUSTRATION FOR FIGURE 4 OMITTED]. Similarly, seedling densities were sharply less in the fall and winter of 1992-1993 than 1991-1992 following a peak annual-grass seedling density in late August of about 750 Bromus japonicus seedlings [m.sup.-2]. Although August precipitation was slightly above normal [ILLUSTRATION FOR FIGURE 1 OMITTED], intensity of rainfall was low with no single rain [greater than]17 mm and no 7 d accumulation [greater than]31 mm. Seedling densities in September 1992 were 20, [less than]2, and 3% of densities in September 1991 for B. japonicus, other annual-grasses and annual forbs, respectively.

Bromus japonicus seedling densities declined 80% between late summer 1992 and early spring 1993 [ILLUSTRATION FOR FIGURE 4 OMITTED]. The 1992-1993 population entering anthesis was only about 8% of the 1991-1992 population for B. japonicus, 2% for other annual grasses and 13% for annual forbs.


The results of this study show that plant species dominance varies in accordance with the variable of assessment. For example, aboveground standing crop was dominated by two perennial grasses, Bouteloua gracilis and Pascopyrum smithii, whereas seed production and seedling emergence were dominated by the annual grass, Bromus japonicus. Other important, subdominant species were: (1) aboveground biomass - B. japonicus and Opuntia polyacantha, a perennial succulent; (2) seed production - Poa secunda and Sporobolus cryptandrus, perennial grasses, Festuca octoflora, an annual grass and Plantago patagonica, an annual forb; and (3) seedling emergence - Festuca octoflora, Pascopyrum patagonica, and two annual forbs, Androsace occidentalis and Hedeoma hispida.

Study data also show that genet production of perennial grasses is meager in comparison with the annual species in this northern mixed-grass prairie community. Still, despite low densities, seedlings of all perennial grass species, except Buchloe dactyloides and Pascopyrum smithii, were observed. These findings are in general agreement with those of Weaver and Mueller (1942) who reported B. dactyloides seedling densities of only 2 [m.sup.-2] in the central Great Plains with no P. smithii seedlings observed. The limited seed production of both Bouteloua gracilis and P smithii, the dominant producers of aboveground biomass in this community, is typical for these species regardless of location (Blake, 1935; Branson, 1941; Riegel, 1941; Brown, 1943). However, B. gracilis seed production (720 filled caryopses [m.sup.-2]) may have been further suppressed in this study as a result of the high clay content of the study site soils ([greater than]20%) as Coffin and Lauenroth (1992) have shown seed production or B. gracilis tends to decrease as clay content of surface soils increases. Also, B. gracilis seedling morphology has been shown to restrict recruitment (Hyder et al., 1971), especially in low soil temperature and/or low soil water potential environments (Briske and Wilson, 1977, 1978; Wilson and Briske, 1979). In the shortgrass prairie region of NE Colorado, it has been shown that B. gracilis rarely, if ever, reproduces from seed (McGinnies et al., 1988). Thus, it can be reasoned that B. gracilis population dynamics are primarily a function of tiller natality and mortality rates (Hyder et al., 1975). Similarly, asexual regeneration via rhizomes is the primary mode of reproduction for P. smithii (Albertson and Weaver, 1944) as seed production is characteristically low and seedling survival rates below average (Mueller and Weaver, 1942). However, Albertson and Weaver (1944) did observe some P. smithii seedlings originating from seed located 5 cm beneath Great Plains' wind-blown soil. Interestingly, we found both B. dactyloides and P. smithii seedlings emerging from incubated seed bank samples collected in these same study sites (pers. obs.) providing evidence of the ability of these species to sexually regenerate.

Field observations of perennial grass seedlings revealed that Bouteloua gracilis, Hesperostipa comata and Schedonnardus paniculatus seedlings were located generally in gaps in the vegetation characterized by bare mineral soil. This is consistent with previous observations by Blake (1935), Weaver and Mueller (1942), Albertson and Weaver (1944) and Costello (1944). More recently, Aguilera and Lauenroth (1993) have provided experimental evidence that successful sexual regeneration of B. gracilis is strongly dependent on the presence of both above- and below-ground gaps in vegetation. However, as reported by Fowler (1986), this type of microsite is not the optimum for all perennial grasses and support for this observation was gleaned from our observations that most Poa secunda seedlings were located within the canopy area of established perennial grasses.

The time of introduction of Bromus japonicus into northern mixed-grass prairie is unclear. Newspaper reports from the Miles City region suggest the presence of annual brome plants (Bromus spp.) was first noted along railroads in the late 1930s. However, it seems reasonable to assume that actual introduction was near the end of the 19th century, the same time as the introduction of Bromus tectorum into the Great Basin region of the U.S. (Mack, 1981). But regardless of time of introduction, neither B. japonicus nor B. rectorum appears to have been prevalent in northern mixed-grass prairies before the 1960s (Black et al., 1937; Ellison, 1960; Reed and Peterson, 1961). Evidence from our study and those of Haferkamp et al. (1994) and Haferkamp et al. (1995), show that seedling emergence of B. japonicus can be environmentally constrained, yet the precipitation threshold in late summer-early fall required to induce Bromus seedling emergence, is apparently less than that for most indigenous annual grasses and forbs. Thus, we hypothesize that availability of suitable microsites permitting sexual regeneration of perennial grasses in northern mixed-grass prairie has been reduced since the arrival of B. japonicus. But we further hypothesize that because Bouteloua gracilis and Pascopyrum smithii, the dominant producers of aboveground biomass in this study, propagate vegetatively and undoubtedly have long lifespans, these species effectively buffer the impacts of B. japonicus on these mixed-grass ecosystems. This is in contrast to the overwhelming successful invasion of B. tectorum into Intermountain West of North America. Mack (1981) speculated "that both long association with herding ungulates and the prominence of the rhizomatous life form among the Great Plains grasses has played a part in their resistence to alien invasion." We believe the results of this study support Mack's hypothesis, and as such, we do not anticipate an ecological shift of northern mixedgrass prairies towards an annual grass dominance.

Acknowledgments. - We thank Keith Klement, Cheryl Murphy and Bryon Bennett for assistance in data collection and Diona Austill for word processing and graphics assistance. This research was conducted trader a cooperative agreement between USDA-ARS and the Montana Agric. Exp. Sta and is published as contribution no. J-2998 from the Montana Agric. Exp. Sta. USDA-Agricultural Research Service, Northern Plains Area, is an equal opportunity/affirmative action employer and all agency services are available without discrimination.

2 See Table 1 for plant nomenclature authorities.


AGUILERA, M. O. AND W. K. LAUENROTH. 1993. Seedling establishment in adult neighborhoods - intraspecific constraints in the regeneration of the bunchgrass Bouteloua gracilis. J. Ecol., 81:253-261.

ALBERTSON, F. W. AND J. E. WEAVER. 1944. Nature and degree of recovery of grassland from the great drought of 1933 to 1940. Ecol. Monogr., 14:393-479.

BLACK, W. H., A. L. BAKER, V. I. CLARK AND O. R. MATHEWS. 1937. Effect of different methods of grazing on native vegetation and gains of steers in Northern Great Plains. USDA Tech. Bull. 547. 18 p.

BLAKE, A. K. 1935. Viability and germination of seeds and early life history of prairie plants. Ecol. Monogr, 5:407-460.

BRANSON, L. R. 1941. An analysis of seed production of native Kansas grasses during the drought of 1939. Trans. Kansas Acad. Sci., 44:116-127.

BRISKE, D. D. AND A. M. WILSON. 1977. Temperature effects on adventitious root development in blue grama seedlings. J. Range Manage., 30:276-280.

----- AND A. M. WILSON. 1978. Moisture and temperature requirements for adventitious root development in blue grama seedlings. J. Range Manage., 31:174-178.

BROWN, H. R. 1943. Growth and seed yields of native prairie plants in various habitats of the mixedprairie. Trans. Kansas Acad. Sci., 46:87-99.

COFFIN, D. P. AND W. K. LAUENROTH. 1992. Spatial variability in seed production of the perennial bunchgrass Bouteloua gracilis (Gramineae). Am. J. Bot., 79:347-353.

COSTELLO, D. F. 1944. Natural revegetation of abandoned plowed land in the mixed prairie association of northeastern Colorado. Ecology, 25:312-326.

COUPLAND, R. T. 1958. The effects of fluctuations in weather upon the grasslands of the Great Plains. Bot. Rev., 24:273-317.

DIX, R. L. 1962. A history of biotic and climatic changes within the North American Grassland, p. 7189. In: Crisp, D. S. (ed.). Grazing in terrestrial and marine environments. Symposium of the British Ecological Society. Blackwell Sci. Pub., Oxford, U.K.

ELLISON, L. 1960. Influence of grazing on plant succession of rangelands. Bot. Rev., 26:1-78.

FOWLER, N. L. 1986. Microsite requirements for germination and establishment of three grass species. Am. Midl. Nat., 115:131-145.

HAFERKAMP, M. R., J. D. VOLESKY, M. M. BORMAN, R. K. HEITSCHMIDT AND P. O. CURRIE. 1993. Effects of mechanical treatments and climatic factors on the productivity of Northern Great Plains rangelands. J. Range Manage., 46:346-350.

-----, M. G. KARL AND M. D. MACNEIL. 1994. Influence of storage, temperature, and light on germination of Japanese brome seed. J. Range Manage., 47:140-144.

-----, D. PALMQUIST, J. A. YOUNG AND M. D. MACNEIL. 1995. Influence of temperature on germination of Japanese brome seed. J. Range Manage., 48:264-266.

HEITSCHMIDT, R. K., S. L. DOWHOWER AND J. W. WALKER. 1987. 14- vs. 42-Paddock Rotational Grazing: Aboveground biomass dynamics, forage production, and harvest efficiency. J. Range Manage, 40:216-223.

-----, E. E. GRINGS, M. R. HAFERKAMP AND M. G. KARL. 1995. Herbage dynamics on 2 Northern Great Plains range sites. J. Range Manage., 48:211-217.

HYDER D. N., A. C. EVERSON AND R. E. BEMENT. 1971. Seedling morphology and seeding failures with blue grama. J. Range Manage., 24:287-292.

HYDER, D. N., R. E. BEMENT, E. E. REMMENGA AND D. F. HERVEY. 1975. Ecological responses of native plants and guidelines for management of shortgrass range. USDA Tech. Bull. 1503.87 p.

KUCHLER, A. W. 1964. The potential natural vegetation of the conterminous United States. Am. Geographical Soc., Pub. 36. New York. 116 p.

LAUENROTH, W. K., D. G. MILCHUNAS, J. L. DODD, R. H. HART, R. K. HEITSCHMIDT AND L. R. RITTENHOUSE. 1994. Grazing in the Great Plains of the United States, p. 69-100 In: Ecological implications of livestock herbivory in the West. Soc. Range Manage., Denver, Colorado.

MACK, R. N. 1981. Invasion of Bromus tectorum L. into western North America: an ecological chronicle. Agro-Ecosystems, 7:145-165.

----- AND D. A. PYKE. 1984. The demography of Bromus tectorum: the role of microclimate, grazing and disease. J. Ecol., 72:731-748.

McGINNIES, W. J., W. A. LAYCOCK, T. TSUCHIYA, C. M. YONKER AND D. A. EDMUNDS. 1988. Variability within a native stand of blue grama. J. Range Manage., 41:391-395.

MILCHUNAS, D. G., O. E. SALA AND W. K. LAUENROTH. 1988. A generalized model of the effects of grazing by large herbivores on grassland community structure. Am. Nat., 132:87-106.

MUELLER, I. M. AND J. E. WEAVER. 1942. Relative drought resistance of seedlings of dominant prairie grasses. Ecology, 23:387-398.

NATIONAL OCEANIC AND ATMOSPHERIC ADMINISTRATION. 1994. Climatic data, Montana annual summary. 1878-1992. Nat. Climatic Data Center, Asheville, North Carolina Vol. 13.43 p.

REED, M. AND R. A. PETERSON. 1961. Vegetation, soil, and cattle responses to grazing on Northern Great Plains range. USDA For. Serv. Tech. Bull. 1252. 79 p.

RIEGEL, A. 1941. Life history and habits of blue grama. Trans. Kansas Acad. Sci., 44:76-83.

WEAVER, J. E. AND I. M. MUELLER. 1942. Role of seedlings in recovery of Midwestern ranges from drought. Ecology, 23:275-294.

WELLS, P. V. 1970. Postglacial vegetational history of the Great Plains. Science, 167:1574-1582.

WHISENANT, S. G. 1990. Changing fire frequencies on Idaho's Snake River Plains: Ecological and management implications, p. 4-10. In: Proc. cheatgrass invasion shrub die-off, and other aspects of shrub biology and management. USDA For. Ser. Inter. Res. Sta. Gen. Tech. Rep. INT-276. 351 p.

WILSON, A. M. AND D. D. BRISKE. 1979. Seminal and adventitious root growth of blue grama seedlings on the central plains. J. Range Manage., 32:209-213.
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Author:Karl, Michael G.; Heitschmidt, R.K.; Haferkamp, Marshall R.
Publication:The American Midland Naturalist
Date:Apr 1, 1999
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