Fire Effects Information System (FEIS)
FEIS Home Page

Index of Species Information

SPECIES:  Miscanthus sinensis

James H. Miller, USDA Forest Service,

Waggy, Melissa A. 2011. Miscanthus sinensis. In: Fire Effects Information System, [Online]. U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station, Fire Sciences Laboratory (Producer). Available: /database/feis/plants/graminoid/missin/all.html [].



Chinese silvergrass
Chinese silver grass
Japanese silver grass
zebra grass

The scientific name of Chinese silvergrass is Miscanthus sinensis Andersson (Poaceae) [24,36,38,50,65,116]. Hitchcock [38] recognizes 3 varieties in the United States:

Miscanthus sinensis var. gracillimus Hitchc. (narrow blades)
Miscanthus sinensis
var. variegatus Beal (blades striped with white)
Miscanthus sinensis var. zebrinus Beal (blades banded or zoned with white)

Various Chinese silvergrass infrataxa occur in Taiwan and Japan ([8], review by [96]).

Under cultivation, Chinese silvergrass is often hybridized with other species of this genus [12], particularly with M. sacchariflorus to create the hybrid Miscanthus × giganteus [49]. More than 50 cultivars of Chinese silvergrass have been introduced to North America since 1980 [70].




SPECIES: Chinese silvergrass
Chinese silvergrass is nonnative to North America. It occurs in "pockets" [31] in most eastern states from Massachusetts south throughout the mid-Atlantic and southeastern states to Florida and across the South to Louisiana. It occurs in several Great Lakes states including Ohio, Michigan, and Illinois and also in Ontario, Canada. In the West, it occurs in Colorado and California [81,108]. Because it is widely used as an ornamental in many parts of North America [71,72,98] and escapes cultivation [40,65,70,77], Chinese silvergrass may occur in other locations in North America. At the time of this writing (2010), Chinese silvergrass was not considered a major invader of wildlands in any area of North America; however, based on invasive species rankings and publications, there appears to be more concern over its spread in the eastern half the United States than in the western half [17,31,61,104,114]. Plants Database provides a distributional map of Chinese silvergrass's North American range.

Chinese silvergrass is native to Asia [36,38,72,98,117]. Its range extends north to the Kuril Islands (Russia) in the subarctic and to the islands of Hokkaido (Japan), south and west throughout the main islands of Japan, the Korean peninsula, eastern China, and to the subtropics in Ryukyu (Japan) and Taiwan ([83], review by [96]). The islands of Habamai and Yuzhno-Sakhalinsk in Russia may be the northern limit of Chinese silvergrass (Shimada and others 1992 cited in [96]).

Although it is unclear exactly when and where Chinese silvergrass was introduced to North America, several floristic surveys from the eastern United States indicated that by the early 1940s, Chinese silvergrass occurred along roadsides, railroad tracks, and many other places in New Jersey [76], Pennsylvania [76,77], and West Virginia [16]. In 1942, Moldenke [76] described Chinese silvergrass as "abundantly naturalized" in Washington, DC. Chinese silvergrass continued to spread in the eastern United States and to other parts of North America, but it is unclear how or when this occurred.

In North America, Chinese silvergrass primarily invades anthropogenically altered sites (see General habitat); there are few examples in the literature of it invading wildlands. Invasive plant guides indicate that Chinese silvergrass invades native grasslands on Cape Cod [112] and in the Upper Great Lakes area [17]. In Maryland, Chinese silvergrass occurred in deciduous woodlands dominated by oaks (Quercus spp.) and other deciduous trees. The woodlands were generally wet to mesic and often occurred near the edges of swamps [95]. Chinese silvergrass occurred but was rare in a longleaf pine (Pinus palustris) ecosystem in the Sandhills region of the southeastern United States [93].

In Japan where it is native, Chinese silvergrass is the dominant species in many grasslands [46,54,83,100,111,113]. One publication estimated that Chinese silvergrass grasslands represented about 25% of all natural or seminatural grassland area in Japan [46]. In Japan, Chinese silvergrass grasslands typically contain a diverse  assemblage of herbaceous species [96]. A 15-year-old Chinese silvergrass-dominated grassland in Japan contained 96 plant species representing 42 families. The upper vegetation stratum (3-7 feet (1-2 m) tall) was comprised solely of Chinese silvergrass; the intermediate stratum (2-3 feet (0.5-1 m) tall) contained several tall herbs, shrubs, lianas, and tree seedlings; and the lowest stratum (0-2 feet (0-0.5 m) tall) contained short herbs and rosettes of taller herbs [78]. Another Chinese silvergrass-dominated grassland in Japan contained about 25 species [83]. Chinese silvergrass grasslands occurring on slopes may have greater species diversity than those on the valley floor (Koyanagi and others 2008 cited in [96]). In some Chinese silvergrass grasslands, dense shade from its leaves may prevent other species from establishing [21], and species diversity may be lower in Chinese silvergrass grassland occurring on degraded sites [83].

Species most commonly associated with Chinese silvergrass grasslands in Japan include western bracken fern (Pteridium aquilinum) ([27,34,35,43,46,83], Koyanagi and others 2008 cited in [96]) and bicolor lespedeza (Lespedeza bicolor) ([35,83,103], Koyanagi and others 2008 cited in [96]), although a variety of other herbaceous species may also be present [6,35,46,83,103,113]. In Chinese silvergrass grasslands, C3 grasses typically dominate in early spring; by summer and fall, dominance shifts to C4 species, including Chinese silvergrass (review by [96]).

In its native range, Chinese silvergrass is occassionally an understory dominant in forest or shrubland. In Japan, Chinese silvergrass occurred in a Japanese red pine (Pinus densiflora) forest [28] and was a characteristic species in a ring-cup oak (Quercus glauca)-Japanese red pine evergreen broadleaf forest [105]. In subtropical Asia, Chinese silvergrass is a codominant groundlayer species in Benguet pine (P. kesiya) forests [27]. In the Philippines, Chinese silvergrass was a dominant ground layer species in a Benguet pine-dominated forest. Its dominance was greatest on slopes around 7,500 feet (2,300 m) in elevation and declined with decreasing elevation [60]. On a slope of an active volcano (last major eruption 1929) in Japan, Chinese silvergrass occurred on bare ground and in shrubland dominated by Miquel's spicywintergreen (Gaultheria miqueliana) and Salix reinii [110].


SPECIES: Miscanthus sinensis
Botanical description: This description covers characteristics that may be relevant to fire ecology and is not meant for identification. Keys for identification are available (e.g., [24,36,36,38,65,87]).

Aboveground: Chinese silvergrass is a perennial [37,84] grass. In North America, Chinese silvergrass is 3 feet (1 m) [87] to 10 feet (3 m) tall [23,36,38,98]. Studies from Japan indicate that Chinese silvergrass does not get taller than 6 feet (2 m) [34,78,100,103,113], but in the Philippines it may grow taller than 10 feet (3 m) [21]. Chinese silvergrass may be taller in warmer climates [14]. A clump of Chinese silvergrass may attain a width equal to its height at maturity [29]. Individual leaf blades are up to 3 feet (1 m) long and from 0.8 inch (2 cm) [38,87] to 4 inches (10 cm) wide [36]. Its flowers occur in a panicle [31,65] that is 6 to 24 inches (20-61 cm) long [31] and consists of an aggregate of racemes 4 to 8 inches (10-20 cm) long [38]. Chinese silvergrass seed collected from a Japanese grassland measured an average of 2.1 mm long × 0.8 mm wide [35].

Belowground: Chinese silvergrass is rhizomatous [14,31,57]. Information pertaining to Chinese silvergrass's underground structure is limited to what is known about it from its native range, primarily Japan. In a grassland where Chinese silvergrass was the second most dominant species, most of the rhizomes were restricted to the top 8 inches (20 cm) of the soil [34]. In another grassland, most Chinese silvergrass rhizomes were in the upper 4 inches (10 cm) of soil, and most of the roots were in the upper 20 inches (60 cm) of soil, although some roots extended as far down as 47 inches (120 cm) (review by [96]).

Fifty percent of Chinese silvergrass's biomass is underground [33]. In Japan, Chinese silvergrass rhizomes branched 3 times/year on average, and 62% of the new branches developed aboveground shoots during that year. The average length of newly branched rhizomes producing shoots was 1.9 inches (4.7 cm) (Matumura and others 1986 cited in [96]).

Stand structure: In Japan, Chinese silvergrass forms distinct patches that may be monoclonal [57]. Shoots within a patch are connected by branching rhizomes. In a grassland in Japan, Chinese silvergrass patches ranged from 1 to 3.75 square feet (915-3,480 cm²) in size and contained 98 to 339 shoots/patch [58]. In another Japanese grassland, the average number of Chinese silvergrass patches in 20-foot² (2 m²) plots was 6.0. The estimated age of the largest patch was 15 years. Chinese silvergrass cover within the plot ranged from 6% to 50% [78]. In an international study of 5 countries, Chinese silvergrass's average shoot density ranged from 57 shoots/m² to 167 shoots/m² [14]. In the Philippines, Chinese silvergrass culms radiate upward and interlock with those of adjacent clumps, often forming a passageway about half a meter high, leaving the ground rather open between clumps. On gentle slopes, Chinese silvergrass may form near monocultures, becoming less dominant on steeper slopes [21]. Reduced light and other resources in the center of a patch causes center shoots to die, resulting in the formation of a 'fairy ring' of surviving peripheral shoots [58,96].

Raunkiaer [88] life form:

Information pertaining to Chinese silvergrass's North American phenology is limited. It is a warm-season grass [37,84]. One nursery publication indicated that 'Gracillimus', a Chinese silvergrass cultivar, flowers in October in Portland, Oregon [29]. Floras from the northeastern United States [65] and North and South Carolina indicate that Chinese silvergrass flowers from September through November [87]. One invasive species manual from the Southeast indicates Chinese silvergrass flowers from August to November and produces seed from September to January [72].

In Japanese grasslands, Chinese silvergrass begins growing in April [78,118] or early May [80,118] and continues through August [51,103,118], or in some locations, into November [57,78]. In the warmer regions of Japan, shoots emerge between June and November [58]. One publication from Japan indicated that Chinese silvergrass flowers from September to October [33]. In Japan, Chinese silvergrass plants occurring at high latitudes or elevations may flower as much as 2 months earlier than those at lower latitudes and elevations (Adati 1958 cited in [96]). Chinese silvergrass undergoes end-of-season shoot senescence [57], and in some locations, culms become yellow and begin to wither in September [118]. Shoots developing late in the season may survive the winter [57].

Chinese silvergrass may undergo seasonal changes in its rhizome carbohydrate reserves. In Japan, carbohydrate content in Chinese silvergrass rhizomes was depleted in June when new shoots were developing [46] but was restored in the fall after plants flowered [45,46].

Chinese silvergrass spreads vegetatively by rhizomes and also by seed (73, review by [96]). In established populations of Chinese silvergrass, very little reproduction occurs from seed [21]. An invasive species manual from the southeastern United States indicated that some cultivars are assumed to be mostly sterile [72].

Pollination and breeding system: Chinese silvergrass is wind pollinated and may be self-incompatible (review by [96], Nishiwaki 1992 cited in [58]); however, an invasive plant guide from New England indicated that many Chinese silvergrass cultivars may self-seed [70]. Seed set percentage may depend on Chinese silvergrass density and distance between plants (review by [96]). One variety of Chinese silvergrass from Taiwan may reproduce by apomixis, while another variety is considered an outcrosser [8].

Seed production: Based on a study from Japan, seed production of individual Chinese silvergrass plants ranged from 64 to 1,051 seeds [33]. In Japanese grasslands, Chinese silvergrass produced 535 [35] to 8,000 seeds/m² (Nishiwaki and others 1996 cited in [96]) and 40,000 to 140,000 seeds/m² in warm areas with high levels of precipitation (Ogato and Nagatoma 1971 cited in [96]). The average weight of Chinese silvergrass seed ranges from 0.87 [79] to 0.96 mg/seed [33].

Seed dispersal: Chinese silvergrass seed is dispersed by wind [21,28,33,70,79,84,85].

Seed banking: In Japan, Chinese silvergrass forms a soil seed bank, but densities may vary depending on the plant community and season. In a Chinese silvergrass-dominated grassland, 80% of the Chinese silvergrass seeds collected from the soil seed bank were viable. The average number of buried Chinese silvergrass seeds in a 3 × 3 × 0.3-foot (1 × 1 × 0.1 m) plot was 875 in the spring and 340 in the summer. In grasslands dominated by other species, the average number of buried Chinese silvergrass seeds in the same size plot was 1,933 seeds in the spring and 1,980 seeds in the summer. In both Chinese silvergrass and Korean lawngrass (Zoysia japonica) grasslands, Chinese silvergrass soil seed bank density was greatest in the first 0.8 inch (2 cm) of soil and declined sharply in samples collected from deeper depths. Chinese silvergrass viable seed density was 10 times greater in the Korean lawngrass stand than in stands dominated by Chinese silvergrass [35].

Vertical soil distribution of Chinese silvergrass seed in Japanese grasslands in 8 plots (10 ×10 × 10 cm²) [35]
Depth (cm)
Average number of Chinese silvergrass seeds

In Japan, soil samples (3 feet² × 4 inches deep (1 m² × 10 cm) ) were taken from three grasslands with average Chinese silvergrass cover of 34.0%, 69.0%, and 76.5%. Grasslands contained an average of 220, 630, and 600 viable Chinese silvergrass seeds/plot, respectively. Samples of the same size collected from a shrubland with 18.7% Chinese silvergrass cover contained an average of 30 viable seeds per sample [111].

The density of viable Chinese silvergrass seed in the soils of various forest communities in southwestern Japan ranged from 0 to 2,238 seeds/0.4 m² plot at a depth of 4 inches (10 cm) and was generally higher in samples collected in fall rather than spring [79].

It is unclear how long Chinese silvergrass seeds stay viable in the soil. In the laboratory, Chinese silvergrass can be stored for at least 1 year without an appreciable loss of viability; the storage method is not critical. However, older seed may have a lower germination rate [9].

Germination: Germination testing indicates that Chinese silvergrass seed may have little dormancy and has a high germination capacity over a wide range of environmental conditions. In several greenhouse and laboratory studies, Chinese silvergrass seed began germinating within 6 days [84], and up to 69% to 100% of its seed germinated in 10 to 25 days [2,4,10,84]. In a laboratory, Chinese silvergrass seed germinated at temperatures from 59 to 90 F° (15-30 °C); optimum temperature was near 77 °F (25 °C). Chinese silvergrass seed germinated in a wide range of pH conditions, ranging from 4.3 to 8.5 [4]. One invasive species manual from the southeastern United States indicated that Chinese silvergrass seed viability may be variable [72].

Seedling establishment and plant growth: Information pertaining to seedling establishment and growth of Chinese silvergrass is limited. Broadcasting Chinese silvergrass seed onto the soil surface produced 15.5 seedlings/m² on average. Chinese silvergrass seedlings emerged within 10 days of being sown but "many" seedlings died from desiccation during the warm, dry conditions that occurred 3 to 4 weeks after sowing [10]. Seedling growth may be inhibited by high (≥8.5) or low (≤4.0) pH, resulting in reduced dry weight [4]. One literature review suggested that in "extremely" acidic soil, Chinese silvergrass may not reproduce by seed [96].

A review of Japanese literature indicated that average aboveground dry matter biomass of Chinese silvergrass ranges from 1.8 t/ha to 21.8 t/ha, although the latter is considered exceptionally high. Warmer climates of Japan may produce higher yields. More research is needed to determine how climate may influence Chinese silvergrass growth [96]. Chinese silvergrass seedlings, grown from seed collected from wild populations in the eastern United States, had an average shoot biomass of 0.08 ounce (2.3 g) and an average height of 17.9 inches (45.4 cm) 15 weeks after seed was planted [71].

Vegetative regeneration: Chinese silvergrass regenerates by sprouting from the rhizomes and by tillering. Rhizomes may aid the recovery of Chinese silvergrass if it is top-killed [35]. Researchers in Japan determined that individual Chinese silvergrass rhizomes survive for at least 3 years; mortality tends to increase for older rhizomes [45]. Under cultivation, however, 5-year-old Chinese silvergrass rhizomes were more productive than rhizomes that were either 1 or 9 years old [9]. Average fresh weight of Chinese silvergrass rhizomes 0 to 7 years old ranged from 7.92 to 31.55 g/0.25 m² and was greatest for rhizomes 1 to 3 years old [45]. Chinese silvergrass annual rhizome production has been estimated to be from 1.3 t/ha to 1.8 t/ha (review [96]). Others have estimated Chinese silvergrass's combined annual rhizome and root production to equal approximately 20% to 25% of its total underground biomass [45]. In a 3-year study of Chinese silvergrass in Japan, tillering occurred 2 to 3 times/year between June and November [57].

Climate: Information pertaining to Chinese silvergrass relationship to climate in North America is limited to 2 localized examples. Chinese silvergrass occurred in a deciduous woodland in Maryland where the regional climate was described as mild temperate and rainy with no distinct dry season; summers were hot and winters mild. The average daily maximum temperature was 67.3 °F (19.6 °C) and average daily minimum temperature was 43 °F (5.9 °C). The warmest month was July and coldest months were January and February. The average total annual rainfall was 45.04 inches (1,144 mm), with the wettest month occurring in August and the driest month in February [95]. Chinese silvergrass occasionally occurred in a longleaf pine ecosystem of the Sandhills region in the southeastern United States that experienced 4 distinct annual seasons. Humid southwestern airflows predominated during late spring and summer, while northwesterly cold fronts alternated with easterly rainy spells during late fall and winter. Fall and spring were the driest seasons. The average winter temperature was 44 °F (6.9 °C), while the average summer temperature was 78.8 °F (26.0 °C). Annual precipitation averaged 47 inches (1,200 mm) of rain plus 3.0 inches (75 mm) of snow [93]. Temperature may influence Chinese silvergrass's elevational distribution (see Elevation).

In Japan, Chinese silvergrass occurs in subarctic, cool-temperate, and warm-temperate climates [83]. It has been reported on sites with annual mean temperatures ranging from 44 °F (6.5 °C) [34,51] to 64.8 °F (18.2 °C) [37,54,57,58,78] and annual mean precipitation ranging from around 47 inches (1,200 mm) [51,78] to 144 inches (3,670 mm) [34,37,54,57,58]. In a 3-year field test across several countries, Chinese silvergrass established and grew on sites where average annual rainfall from April to September ranged from 5.79 inches (147 mm) to 18.1 inches (459 mm) [14].

Tests performed in Europe indicate that Chinese silvergrass hybrids are tolerant of cold, although level of cold tolerance may vary between cultivars. Chinese silvergrass had greater tolerance of frost than other species of Miscanthus, which was attributed to lower moisture content in its rhizomes [11]. In field tests in Denmark and Sweden, Chinese silvergrass rhizomes survived winter soil temperatures below 24 °F (-4.5 °C) [14].

Elevation: Chinese silvergrass occurs at elevations <700 feet (200 m) in California [36]. At a National Historic Site in North Carolina, Chinese silvergrass occurred at a low elevations [115]. In Japan, Chinese silvergrass has been reported from 1,000 (400 m) [80] to 5,900 feet ( 1,800 m) [34,74,110].

A literature review indicated that elevation may influence Chinese silvergrass's growth and development [96]. Hayashi and Hishinuma [34] considered 4,300 feet (1,300 m) to be near the limits of Chinese silvergrass's distribution in Sagadaira, Japan. At this elevation, growth may not be sufficient to form monocultures [34]. Other reports from Japan indicate that Chinese silvergrass occurred at elevations from 5,410 to 5,810 feet (1,650-1,770 m) but dominated only around 5,410 feet (1,650 m). Researchers attributed lower cover of Chinese silvergrass at higher elevations to a reduction in mean annual temperature [74]. In the Philippines, Chinese silvergrass dominated the groundlayer vegetation at elevations from 5,380 to 7,500 feet (1,640-2,300 m). Its dominance declined at lower elevations and in valley grasslands [60].

General habitat: In North America, Chinese silvergrass occurs primarily in anthropogenically altered sites such as previously cultivated fields, vacant lots, yards, gardens, irrigation ditches, along roadsides and railroad tracks, and near old home sites and cemeteries [19,32,36,65,69,70,75,76,87,93,107]. It occasionally occurs in wildlands or on the fringe of wildlands in deciduous woodlands [95], coniferous forests [93], forest clearings [31,99], and in grasslands [17,70,112].

Substrate and pH: In Japan, Chinese silvergrass occurs in most soil textures ([47,54], Jinno and Umeno 1995 cited in [96]). In one study, Chinese silvergrass occurred in mountain grasslands that contained a thick humus layer [118]. Chinese silvergrass grasslands may occur on volcanic ash or volcanic ash-like soil [53,118]. On these sites, large amounts of dead plant material, produced by dying Chinese silvergrass, is incorporated into soil organic matter each year [53,91,92,118].

Available information indicates that Chinese silvergrass prefers moist but not saturated soils. A nursery publication from Oregon stated that the cultivar 'Gracillimus' tolerates wet soil but prefers well-drained soil [29]. One study from Japan claimed that Chinese silvergrass does not grow well where the A horizon is shallow and the amount of moisture in the soil is relatively low [51]. Soil moisture content in Chinese silvergrass-dominated riparian communities in Japan ranged from 14% to 25% (Jinno and Umeno 1995 cited in [96]). In another Chinese silvergrass grassland in Japan, moisture content for the A, B, and C horizons ranged from 46% to 52% [34]. In the Philippines, Chinese silvergrass occurred near a bog but did not readily invade areas that were inundated with water for part or all of the year [21]. In a pine forest in the Philippines, Chinese silvergrass occurred on moist "protected" sites [60]. Chinese silvergrass hybrids are being developed to improve drought tolerance [13].

Chinese silvergrass occurs in a wide range of soil acidities. In Japan, Chinese silvergrass grasslands have soil pH from 3.8 [52,53] to 6.5 [26,34,52,53,100]; however, seedling establishment may be inhibited on sites with very low or high pH (see Seedling establishment and plant growth). Soils in Chinese silvergrass grasslands may be slightly more acidic in the B and C horizons than in the A horizon [34]. On sites where Chinese silvergrass distribution was scattered, soil pH ranged from 2.7 to 6.8 [2]. In eastern Asia, Chinese silvergrass excretes citric acid, allowing it to grow in acidic soils containing high concentrations of aluminum [52]. In Japan, Chinese silvergrass is a dominant species in acidic volcanic ash soils [118]. Landscapers from Portland, Oregon, recommend that Chinese silvergrass cultivars be planted in slightly acidic soil, preferably enriched with organic material [29].

Shade tolerance: Available evidence at the time of this publication (2010) indicates that Chinese silvergrass grows in full sun but tolerates at least some shade. An invasive species guide from Massachusetts stated that Chinese silvergrass grows in full sun [66]. Landscapers in the Portland, Oregon, recommend that Chinese silvergrass cultivars be planted in full sun to slight shade [29]. One invasive species publication from the southeastern United States stated that Chinese silvergrass is shade tolerant [72]. In southeastern Kentucky, Chinese silvergrass is commonly found in secondary Cumberland Plateau woodlands [68]. In Japan, Chinese silvergrass was the second most dominant species on a site shaded by a 49-foot (15 m) tall Japanese-cedar (Cryptomeria japonica). The maximum light intensity at that site was 67% (even at the most unshaded time of the season) compared to a sunny site that was not shaded [59]. In a pine forest in the Philippines, Chinese silvergrass cover was unaffected by canopy cover [60].

Potential successional stages: In Japan, Chinese silvergrass-dominated grasslands are typically considered seral stages in secondary succession [83] that eventually transition to forests [25,26,35,51,78,80,83] or Korean lawngrass-dominated grasslands (Itow 1962 cited in [96]). In the absence of fire, Chinese silvergrass grasslands have converted to forest within 20 [26] to 100 [25] years.

In Japan, Chinese silvergrass establishes during early stages of secondary succession [85] in young tree plantations [37] or forest clearcuts [45]. Chinese silvergrass may also establish in grasslands shortly after pioneering short-grass species begin to decline [83]. Chinese silvergrass also establishes during the initial stages of primary succession [33] or during early secondary succession on volcanic sites [100]. Once established, Chinese silvergrass grasslands may persist for several decades or even for a century before transitioning to other communities (Sakanoue 2001 cited in [96]).

Available evidence suggests that successional changes in Chinese silvergrass may be influenced by habitat and resource availability. In Japan, the relative dominance of Chinese silvergrass in plant communities increased faster on ridge and slope habitats compared to valley habitat, leading researchers to speculate that resource availability in different habitat types and/or topographical features may influence Chinese silvergrass's growth and its subsequent successional patterns [85]. In Chinese silvergrass grasslands in the Philippines, dense shade from Chinese silvergrass leaves may prevent later-successional species from establishing [21], particularly pine seedlings [60]. Researchers in Japan speculated that seasonal changes in light availability in Chinese silvergrass grasslands may influence the establishment and subsequent growth of tree seedlings [103]. On abandoned ski slopes in Japan, tree seedlings established better in patches of Chinese silvergrass than in patches of other native and nonnative grasses, leading Tsuyuzaki [106] to speculate that Chinese silvergrass grasslands may facilitate successional transitions toward forest. In the Philippines, Chinese silvergrass surrounding bogs may eventually dominate the bogs if standing water is drained [21].

In Japan and the Philippines, most Chinese silvergrass grasslands are artificially maintained as "subclimax" communities by mowing, grazing, and burning [21,25,26,35,46,78,80,82,83], with 2 exceptions. On volcanic soils, Chinese silvergrass dominated "subclimax" grasslands under "natural" conditions [118]. Chinese silvergrass grasslands occurring at high elevations above the tree line may persist in late succession without human intervention [83].


SPECIES: Miscanthus sinensis

Immediate fire effect on plant: Several studies from Japan suggest that Chinese silvergrass is generally top-killed by fire [28,35,46,47]; however, its rhizomes typically survive (see Fire adaptations). In experimental plots, 0% to 83% of Chinese silvergrass culms were top-killed by spring and early summer prescribed fire [46]. Spring fire may have less immediate impact on Chinese silvergrass than summer fire, particularly in areas where it does not fully emerge until May. Fire temperature may influence the percent of Chinese silvergrass culms top-killed by fire (see Plant response to fire).

Postfire regeneration strategy [97]:
Rhizomatous herb, rhizome in soil
Tussock graminoid

Fire adaptations and plant response to fire:
Fire adaptations: Chinese silvergrass survives fire primarily because of its ability to sprout from rhizomes [28,35,46,47] and tillering [46,47], but it may also establish from seed after fire [28]. One study from Japan indicated that when aboveground culms of Chinese silvergrass are destroyed by fire or mowing, regeneration occurs primarily from rhizomes rather than from seed [35]. Chinese silvergrass regenerated from both rhizomes and seeds in a Japanese red pine forest after a March prescribed fire; however, postfire regeneration was substantially greater from rhizomes (average 0.62 rhizome sprout/m²) than from seed ( average 0.02 seedling/m²) [28].

Plant response to fire: Information available as of 2010 suggests Chinese silvergrass responds favorably to fire. One invasive plant publication from the southeastern United States indicated that Chinese silvergrass establishes and spreads easily , particularly after burning [72]. In Japan, Chinese silvergrass grasslands are maintained with regular annual burning [26,46,80,92]. A regression model developed for pine forests and grasslands in the Philippines indicated that Chinese silvergrass's importance tended to increase with time since fire. In a pine forest, Chinese silvergrass dominated the ground vegetation, which had not burned for over 5 years; however, Kowal [60] speculated that that if fire continued to be excluded, most of the pine forest and adjacent grassland would eventually be replaced by montane forest species.

Studies from Japan suggest that fire may increase tillering [46,47], accelerate leaf emergence, and increase photosynthetic rates [47] in Chinese silvergrass. Fujita [20] observed increased chlorophyll content in Chinese silvergrass after fire and attributed it to postfire increases in soil nitrogen. A survey from the Philippines suggested that fire facilitates Chinese silvergrass growth by "opening up the vegetation and restoring ashes to the ground" [21]. One review indicated that charred residues of Chinese silvergrass contribute to the accumulation of humus on some sites in Japan [96].

Fire may damage Chinese silvergrass culms (see Immediate fire effect on plant), but plants typically recover quickly by tillering and sprouting from rhizomes. In a Chinese silvergrass grassland burned in April or May (when Chinese silvergrass's rhizome starch reserves are high and culms are not fully emerged (see Seasonal Development)), tillering was 2 to 4 times greater in burned plots than in the unburned plot. By fall of the same year, Chinese silvergrass abundance (based on height, dry weight, or culm number) on burned plots was nearly equal to that on the unburned plot [46,47]. In plots burned in June of that same year, Chinese silvergrass recovery was slower, but by the next growing season, the number of Chinese silvergrass culms exceeded those observed in plots burned in April or May [46].

Fire may not favor Chinese silvergrass in all instances. In Japan, a Chinese silvergrass-dominated grassland transitioned to a bicolor lespedeza stand after being burned repeatedly in early spring [35]. In another Chinese silvergrass grassland, Chinese silvergrass persisted on a site that had been burned annually; however, its growth was greater on unburned sites than on burned sites [80].

FUELS AND FIRE REGIMES: Fuels: Invasive plant publications from southeastern United States indicate that Chinese silvergrass is considered highly flammable and a fire hazard [18,72,99]. A survey from the Philippines suggested that Chinese silvergrass provides abundant "material" for fire [21]. In Japan, annual prescribed fire consumes dead [27,78] Chinese silvergrass culms and litter [25]. Chinese silvergrass litter is typically greatest in May when plant material from the previous growing season has accumulated. Its litter decomposes gradually over the growing season, reaching its lowest abundance in October [34]. In an experimental Chinese silvergrass grassland in Japan, the amount of dried grasses and litter before fire ranged from 330 g/m² to 950 g/m². Prior to burning, the fuel was "pushed down" to resemble early spring conditions and spread out to <20 inches (40 cm) above the soil surface. The fire's spread rate ranged from 0.5 to 4.0 m/minute in fall fires, and from 0.7 to 1.4 m/minute in spring fires [46]. In another Chinese silvergrass grassland in Japan, "fire ran quickly on the soil surface" [92].

In subtropical Asia, Chinese silvergrass is a codominant groundlayer species in Benguet pine forests. During the dry season, cured grasses and pine litter favor the spread of surface fires, which tend to kill pine seedlings and other fire-sensitive vegetation. Pine stands with fires at short intervals (1-3 years) had little pine regeneration (Goldammer 1985 cited in [27]).

Fire regimes: Because little has been described about what types of plant communities are most vulnerable to Chinese silvergrass invasion in North America, it is unclear what fire regimes it is associated with or how it may influence fire regimes in North America. D'Antonio and others [18] speculated that the most "significant" effect of invasion by nonnative grasses in general is the potential of nonnative grasses to increase fire frequency and perhaps intensity because these grasses provide the fine fuels necessary for the initiation and propagation of fire [18]. NatureServe [81] suggested that Chinese silvergrass may alter fire regimes in plant communities it invades but provided no details or examples.

In Japan, Chinese silvergrass grasslands are maintained by annual prescribed fire [25,78,80], suggesting it is adapted to frequent fire. In subtropical Asia, Chinese silvergrass is a codominant groundlayer species in Benguet pine forests where fire may occur every 1 to 3 years; however, it is unclear if these fires are wild or prescribed. In this plant community, fire intensity and severity vary according to fire frequency. Annual fires usually consume dead organic matter including grasses. Where fire is excluded for long periods, wildfires tend to be of "extreme intensity" due to high fuel accumulation. Most fires take place during the dry season from the middle of January until May [27].

As of this writing (2010), detailed information on fire intensity and severity in areas where Chinese silvergrass occurs was limited to prescribed fires used to maintain Chinese silvergrass grasslands in Asia. Average fire temperatures and flame heights were measured for prescribed fires in a Chinese silvergrass grassland in Japan. Average fire temperature was greatest for spring fire, while average flame height was highest for fall fire. A complete list of fire temperatures and flame heights, weather, air temperature, wind spread and direction, fuel load, and rate of spread for individual fires is provided in the publication [47]. In another Chinese silvergrass grassland in Japan, charred plant material and half-charred plants were scattered over an area that had undergone a prescribed fire [92], suggesting low to moderate fire severity.

See the Fire Regime Table for further information on fire regimes of vegetation communities in which Chinese silvergrass may occur. Find further 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".

In its native range, Chinese silvergrass is well adapted to fire and responds favorably after being burned (see Plant response to fire). In Japan, prescribed fire is used to maintain Chinese silvergrass grasslands by preventing encroachment of native woody species [26,54,78,80] and reducing accumulated litter ([25], review by [96]).

Information pertaining to the use of prescribed fire on Chinese silvergrass infestations outside its native range is lacking. Based on Chinese silvergrass's response to fire in its native range and a few observations from North America [18,72,99], it seems likely that existing populations of Chinese silvergrass would persist and potentially spread after fire, even on sites were Chinese silvergrass was not currently dominant. However, because Chinese silvergrass does not establish readily by seed and many Chinese silvergrass cultivars are thought to be sterile (see Regeneration Processes and Fire adaptations), the ability of Chinese silvergrass to spread onto burns where it did not previously occur may be limited.

Altered fuel characteristics: As of this writing (2010), information pertaining to Chinese silvergrass potential to alter fuel characteristics was lacking. However, grasses and grass-dominated systems in general provide fine fuels necessary for the initiation and propagation of fire [18].


SPECIES: Miscanthus sinensis

Information on state-level noxious weed status of plants in the United States is available at Plants Database.

One study indicated that reintroduced elk in Kentucky used Chinese silvergrass for forage, primarily in the summer and occasionally in the fall [90]. Based on its palatability to cattle, domestic goats, and domestic sheep, Vermont researchers speculated that Chinese silvergrass could be used as livestock forage in northern temperate regions [5].

In Korea and western Japan, Chinese silvergrass has been used for domestic livestock feed [37,41].

In Korea and Japan, birds use Chinese silvergrass for nesting [41,56]. A literature review gives a detailed description of Chinese silvergrass importance to wildlife in its native range of Japan, including its use by invertebrates [96]. Preliminary studies suggest that grasshoppers may influence the productivity of Chinese silvergrass grasslands [80]; however, in another study grasshoppers had little effect on the primary production of Chinese silvergrass [67].

Palatability and/or nutritional value: A literature review indicates that that Chinese silvergrass may be highly palatable to livestock [96]. In one study, cattle in Japan preferred Chinese silvergrass over other available grasses and herbs [37].

Cover value: No information is available on this topic.

In North America, Chinese silvergrass is widely sold as an ornamental grass for landscaping [17,71,72]. In Mississippi, it has been recommended for use as a vegetative hedge [64].

A literature review indicated that in its native range, Chinese silvergrass culms have been used for roof thatching on traditional buildings. It is used to make yellow dye and storage bags for charcoal. In Japan, Chinese silvergrass is used to stabilize easily erodible soils [96] and is planted to revegetate abandoned ski slopes [106].

Because Chinese silvergrass is highly productive and uses nutrients and water efficiently, it has been identified as a potential biomass energy crop [9,49]. Of particular interest is the sterile triploid Chinese silvergrass hybrid Miscanthus × giganteus [49]. In Europe, Chinese silvergrass has been evaluated as a potential fuel for electricity production [42]. In Korea and western Japan, it has been used for organic fertilizer [37,41].

Impacts: Available evidence suggests that Chinese silvergrass may be invasive in some areas of North America; however, to what degree it impacts native plant communities and ecosystems is unclear. One greenhouse study determined that Chinese silvergrass grows well when planted with switchgrass (Panicum virgatum) [71]—a common and "aggressive" grass native to North American tallgrass prairies [38]—suggesting Chinese silvergrass may displace native grasses if it establishes in tallgrass prairies [71]. Based on Chinese silvergrass's popularity as an ornamental grass in the United States and its potential to become invasive in some situations, NatureServe [81] has given Chinese silvergrass an invasive species ranking of medium. Species given this ranking pose a moderate threat to native species and ecological communities [81].

Chinese silvergrass was indentified as one of a dozen invasive plants that land managers in the southern Appalachian states are most concerned about [61], and it is listed as invasive or potentially invasive in 6 southeastern states: Alabama [1], Georgia [22], Kentucky [55], Missouri [73], South Carolina [94], and Tennessee [104]. In Kentucky, Chinese silvergrass is considered a potential threat to whitehair goldenrod (Solidago albopilosa), an endemic in the Red River Gorge [114] that is federally listed as threatened [109]. Chinese silvergrass is considered potentially invasive in Connecticut [15] and forms large clumps that may displace native species throughout New England [70]. An invasive plant guide from the upper Great Lakes states indicates that Chinese silvergrass is a minor invader in wildlands, particularly grasslands [17]. In its native range, Chinese silvergrass is considered a weed on disturbed sites [89] and in tree plantations, where it suppresses planted saplings if not controlled [37].

In addition to displacing native plants, Chinese silvergrass may have other ecological impacts. Chinese silvergrass litter decomposes slowly (Matumura and others 1986 [96]), which may slow the return of nutrients to the soil, particularly in the absence of fire [96]. NatureServe [81] suggested that Chinese silvergrass may alter fire regimes in plant communities where it invades but gave no examples of this occurring.

Chinese silvergrass hybrids are being developed that produce high yields [9,12] and are tolerant to cold [11] or drought [13]. Introduction of these hybrids to North America could potentially increase Chinese silvergrass's spread.

Control: As of this writing (2010), information pertaining to Chinese silvergrass control in North America was limited to a few generalizations made regarding the use of physical or chemical controls. Researchers in Japan have had some success at controlling Chinese silvergrass through the use of livestock grazing (see Biological control).

Fire: For information on the use of prescribed fire to control this species, see Fire Management Considerations.

Prevention: Because Chinese silvergrass spreads vegetatively, it is best not to plant it adjacent to wildland areas. Sterile varieties are being developed to reduce its spread [9], but vegetative reproduction will likely be possible from these populations.

Cultural control: No information is available on this topic.

Physical or mechanical control: An Internet publication from the Mid-Atlantic states indicated that Chinese silvergrass may be controlled by hand-pulling seedlings and shallow-rooted plants. Swearingen and others [99] recommended that larger plants be dug out, including the entire root system, to prevent vegetative sprouting, and cautioned that mowing Chinese silvergrass may spread plants into new areas. An invasive plant guide from the upper Great Lakes states suggested manual or mechanical removal of Chinese silvergrass but provided no details on these methods [17].

In Japan, mowing is the most common practice used to control Chinese silvergrass in plantations [37]. One literature review indicated that mowing Chinese silvergrass grasslands 3 times/year decreased Chinese silvergrass's annual biomass production from 7.1 to 0.75 t/ha and reduced its height from 33 inches (85 cm) to 15 inches (38 cm) [96]; however, the source of this information was unclear.

Biological control: Widespread use of Chinese silvergrass as an ornamental makes it unlikely that a biological control will be developed for this species. Additionally, many ornamental plants, particularly Chinese silvergrass, are chosen because they have few biological enemies [101].

Studies from Japan indicate that Chinese silvergrass may have a low tolerance to livestock grazing ([37,113], review by [96]). In Japan, livestock preferred newly developing leaves of Chinese silvergrass, which have high photosynthetic capacity and contain high concentrations of nitrogen. Chinese silvergrass generally declines and vegetation dominance shifts to other species when livestock graze it (review by [96]). On a tree plantation in Japan, 4 years of livestock grazing reduced the average size of Chinese silvergrass plants. After the initial grazing season (190 days), the proportion of undefoliated Chinese silvergrass clumps and shoots "rapidly" decreased, leaving approximately 20% of clumps and 10% of shoots intact. Researchers concluded that cattle grazing could potentially control Chinese silvergrass in tree plantations but recommended further study to determine optimum grazing intensity [37].

Chemical control: One invasive plant publication suggested that periodic spot spraying with glyphosate beginning in spring—when the new shoots are 4 to 6 inches (10-15 cm) tall—until fall when the plants flower, may control Chinese silvergrass [31]. An invasive plant publication from the upper Great Lakes states indicated that a fall or late spring application of glyphosate controlled Chinese silvergrass [99]. The Tennessee Exotic Pest Plant Council [104] recommended a combination of imazapyr and glyphosate treatments in the fall for Chinese silvergrass control. Continued spot treatments may be necessary to kill new rhizome sprouts [31,104].

Integrated management: No information is available on this topic.


SPECIES: Miscanthus sinensis
The following table provides fire regime information that may be relevant to Chinese silvergrass habitats. Find further 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".

Fire regime information on vegetation communities in which Chinese silvergrass may occur. This information is taken from the LANDFIRE Rapid Assessment Vegetation Models [63], which were developed by local experts using available literature, local data, and/or expert opinion. This table summarizes fire regime characteristics for each plant community listed. The PDF file linked from each plant community name describes the model and synthesizes the knowledge available on vegetation composition, structure, and dynamics in that community. Cells are blank where information is not available in the Rapid Assessment Vegetation Model.
Great Lakes Northeast Southeast
Great Lakes
Vegetation Community (Potential Natural Vegetation Group) Fire severity* Fire regime characteristics
Percent of fires Mean interval
Minimum interval
Maximum interval
Great Lakes Grassland
Mosaic of bluestem prairie and oak-hickory Replacement 79% 5 1 8
Mixed 2% 260    
Surface or low 20% 2   33
Vegetation Community (Potential Natural Vegetation Group) Fire severity* Fire regime characteristics
Percent of fires Mean interval
Minimum interval
Maximum interval
Eastern woodland mosaic Replacement 2% 200 100 300
Mixed 9% 40 20 60
Surface or low 89% 4 1 7
Oak-pine (eastern dry-xeric) Replacement 4% 185    
Mixed 7% 110    
Surface or low 90% 8    
Northeast Forested
Appalachian oak forest (dry-mesic) Replacement 2% 625 500 >1,000
Mixed 6% 250 200 500
Surface or low 92% 15 7 26
Vegetation Community (Potential Natural Vegetation Group) Fire severity* Fire regime characteristics
Percent of fires Mean interval
Minimum interval
Maximum interval
Southeast Woodland
Longleaf pine/bluestem Replacement 3% 130    
Surface or low 97% 4 1 5
Longleaf pine (mesic uplands) Replacement 3% 110 40 200
Surface or low 97% 3 1 5
Longleaf pine-Sandhills prairie Replacement 3% 130 25 500
Surface or low 97% 4 1 10
*Fire Severities
Replacement: Any fire that causes greater than 75% top removal of a vegetation-fuel type, resulting in general replacement of existing vegetation; may or may not cause a lethal effect on the plants.
Mixed: Any fire burning more than 5% of an area that does not qualify as a replacement, surface, or low-severity fire; includes mosaic and other fires that are intermediate in effects.
Surface or low: Any fire that causes less than 25% upper layer replacement and/or removal in a vegetation-fuel class but burns 5% or more of the area [30,62].


SPECIES: Miscanthus sinensis
1. Alabama Invasive Plant Council. 2007. List of Alabama's invasive plants by land-use and water-use sectors. Alabama Invasive Plant Council (Producer). Available: [2009, January 5]. [72714]
2. An, Gi-Hong; Miyakawa, Sachie; Kawahara, Ai; Osaki, Mitsuru; Ezawa, Tatsuhiro. 2008. Community structure of arbuscular mycorrhizal fungi associated with pioneer grass species Miscanthus sinensis in acid sulfate soils: habitat segregation along pH gradients. Soil Science and Plant Nutrition. 54: 517-528. [80078]
3. Asher, Jerry; Dewey, Steven; Olivarez, Jim; Johnson, Curt. 1998. Minimizing weed spread following wildland fires. In: Christianson, Kathy, ed. Proceedings, Western Society of Weed Science; 1998 March 10-12; Waikoloa, HI. In: Western Society of Weed Science. 51: 49. Abstract. [40409]
4. Aso, Takeo. 1976. Studies on the germination of seeds of Miscanthus sinensis Anderss. Science Reports of the Yokohama National University. Section II: Biological and Geological Sciences. 23: 27-37. [80148]
5. Bae, Dong Ho; Gilman, B. E.; Welch, J. G.; Palmer, R. H. 1983. Quality of forage from Miscanthus sinensis. Journal of Dairy Science. 66(3): 630-633. [80098]
6. Beerling, David J.; Bailey, John P.; Conolly, Ann P. 1994. Biological flora of the British Isles: Fallopia japonica (Houtt.) Ronse Decraene (Reynoutria japonica Houtt.; Polygonum cuspidatum Sieb. & Zucc.). Journal of Ecology. 82(4): 959-979. [77586]
7. Bussan, Alvin J.; Dyer, William E. 1999. Herbicides and rangeland. In: Sheley, Roger L.; Petroff, Janet K., eds. Biology and management of noxious rangeland weeds. Corvallis, OR: Oregon State University Press: 116-132. [35716]
8. Chou, Chang-Hung; Chiang, Yu-Chung; Chiang, Tzen-Yuh. 2000. Genetic variability and phytogeography of Miscanthus sinensis var. condensatus, an apomictic grass, based on RAPD fingerprints. Canadian Journal of Botany. 78: 1262-1268. [80149]
9. Christian, D. G.; Yates, N. E.; Riche, A. B. 2003. Evaluating grasses as a long-term energy resource. Oxfordshire, UK: Department of Trade and Industry: 46 p. [80152]
10. Christian, D. G.; Yates, N. E.; Riche, A. B. 2005. Establishing Miscanthus sinensis from seed using conventional sowing methods. Industrial Crops and Products. 21(1): 109-111. [80100]
11. Clifton-Brown, J. C.; Lewandowski, I. 2000. Overwintering problems of newly established Miscanthus plantations can be overcome by identifying genotypes with improved rhizome cold tolerance. New Phytologist. 148(2): 287-294. [79838]
12. Clifton-Brown, J. C.; Lewandowski, I. 2002. Screening Miscanthus genotypes in field trials to optimise biomass yield and quality in southern Germany. European Journal of Agronomy. 16: 97-110. [80153]
13. Clifton-Brown, J. C.; Lewandowski, I.; Bangerth, F.; Jones, M. B. 2002. Comparative responses to water stress in stay-green, rapid- and slow senescing genotypes of the biomass crop, Miscanthus. New Phytologist. 154(2): 335-345. [79839]
14. Clifton-Brown, John C.; Lewandowski, Iris; Andersson, Bengt; Basch, Gottleib; Christian, Dudley G.; Kjeldsen, Jens Bonderup; Jorgensen, Uffe; Mortensen, Jorgen V.; Riche, Andrew B.; Schwarz, Kai-Uwe; Tayebi, Koeyumars; Teixeira, Fernando. 2001. Performance of 15 Miscanthus genotypes of five sites in Europe. Agronomy Journal. 93: 1013-1019. [80154]
15. Connecticut Invasive Plant Working Group. 2009. Connecticut invasive plant list, July 2009, [Online]. In: Connecticut invasive plant list. Storrs, CT: University of Connecticut, Connecticut Invasive Plant Working Group (Producer). Available: [2010, January 25]. [78290]
16. Core, Earl L. 1941. Notes on some West Virginia plants. Castanea. 6(5): 86-88. [79933]
17. Czarapata, Elizabeth J. 2005. Invasive plants of the Upper Midwest: An illustrated guide to their identification and control. Madison, WI: The University of Wisconsin Press. 215 p. [71442]
18. D'Antonio, Carla M.; Vitousek, Peter M. 1992. Biological invasions by exotic grasses, the grass/fire cycle, and global change. Annual Review of Ecology and Systematics. 23: 63-87. [20148]
19. DuMond, David M. 1970. Floristic and vegetational survey of the Chattooga River Gorge. Castanea. 35(4): 201-244. [79896]
20. Fujita, Hiroko. 1987. The effect of fire on soil nitrogen mineralization and chlorophyll contents of Miscanthus sinensis. Ecological Review. 21(2): 87-91. [80105]
21. Gates, Frank C. 1915. A sphagnum bog in the tropics. Journal of Ecology. 3(1): 24-30. [79859]
22. Georgia Exotic Pest Plant Council. 2006. List of non-native invasive plants in Georgia, [Online]. Southeast Exotic Pest Plant Council (Producer). Available: [2009, January 5]. [72787]
23. Gilman, Elizabeth M. 1957. Grasses of the Tidewater-Piedmont region of northern Virginia and Maryland. Castanea. 22(1): 1-105. [79966]
24. Gleason, Henry A.; Cronquist, Arthur. 1991. Manual of vascular plants of northeastern United States and adjacent Canada. 2nd ed. New York: New York Botanical Garden. 910 p. [20329]
25. Golchin, A.; Baldock, J. A.; Clarke, P.; Higashi, T.; Oades, J. M. 1997. The effects of vegetation and burning on the chemical composition of soil organic matter of a volcanic ash soil as shown by C-13 NMR spectroscopy. II. Density fractions. Geoderma. 76: 175-192. [79970]
26. Golchin, A.; Clarke, P.; Baldock, J. A.; Higashi, T.; Skjemstad, J. O.; Oades, J. M. 1997. The effects of vegetation and burning on the chemical composition of soil organic matter in a volcanic ash soil as shown by C-13 NMR spectroscopy. I. Whole soil and humic acid fraction. Geoderma. 76(3-4): 175-192. [80085]
27. Goldammer, J. G.; Penafiel, S. R. 1990. Fire in the pine-grassland biomes of tropical and subtropical Asia. In: Goldammer, J. G., ed. Fire in the tropical biota: ecosystem processes and global challenges. Berlin: Springer-Verlag: 53-64. [53281]
28. Goto, Yoshiaki; Yoshitake, Takashi; Okano, Michiaki; Shimada, Kazunori. 1996. Seedling regeneration and vegetative resprouting after fires in Pinus densiflora forests. Vegetatio. 122(2): 157-165. [75829]
29. Graydon, Charlotte B. 1989. Field notes: Miscanthus sinensis 'Gracillimus'. American Nurseryman. 169(10): 118. [80104]
30. Hann, Wendel; Havlina, Doug; Shlisky, Ayn; [and others]. 2010. Interagency fire regime condition class (FRCC) guidebook, [Online]. Version 3.0. In: (Frames Fire Research And Management Exchange System). National Interagency Fuels, Fire & Vegetation Technology Transfer (NIFTT) (Producer). Available: [81749]
31. Haragan, Patricia Dalton. 1996. Miscanthus sinensis--Chinese silver grass, eulalia. In: Randall, John M.; Marinelli, Janet, eds. Invasive plants: Weeds of the global garden. Handbook #149. Brooklyn, NY: Brooklyn Botanic Garden: 89. [73459]
32. Harrelson, Sarah M.; Cantino, Philip D. 2006. The terrestrial vascular flora of Strounds Run State Park, Athens County, Ohio. Rhodora. 108(934): 142-183. [72485]
33. Hayashi, I. 1979. Ecology, phytosociology and productivity of grasses and grasslands: The autecology of some grassland species. Numata, Makoto, ed. Ecology of grasslands and bamboolands in the world. Boston: Dr. W. Junk B. V.: 141-152. [80158]
34. Hayashi, I.; Hishinuma, Y.; Yamasawa, T. 1981. Structure and functioning of Miscanthus sinensis grassland in Sugadaira, central Japan. Vegetatio. 48(1): 17-25. [79828]
35. Hayashi, Ichiroku; Numata, Makoto. 1971. Viable buried-seed population in the Miscanthus and Zoysia type grasslands in Japan--Ecological studies on the buried-seed population in the soil related to plant succession: IV. Japanese Journal of Ecology. 20(6): 243-252. [80159]
36. Hickman, James C., ed. 1993. The Jepson manual: Higher plants of California. Berkeley, CA: University of California Press. 1400 p. [21992]
37. Hirata, Masahiko; Hasegawa, Nobumi; Nogami, Kangoro; Sonoda, Tatsunobu. 2007. Evaluation of forest grazing as a management practice to utilize and control Miscanthus sinensis in a young tree plantation in southern Kyushu, Japan. Grassland Science. 53: 181-191. [80161]
38. Hitchcock, A. S. 1951. Manual of the grasses of the United States. Misc. Publ. No. 200. Washington, DC: U.S. Department of Agriculture, Agricultural Research Administration. 1051 p. [2nd edition revised by Agnes Chase in two volumes. New York: Dover Publications, Inc.]. [1165]
39. Hobbs, Richard J.; Humphries, Stella E. 1995. An integrated approach to the ecology and management of plant invasions. Conservation Biology. 9(4): 761-770. [44463]
40. Hockenberry, Mary; Paul, Joe. 2005. Miscanthus sinensis and Panicum virgatum competition study. HortScience. 40(4): 1106-1106. [80083]
41. Hong, Sun-Kee; Nakagoshi, Nobukazu; Kamada, Mahito. 1995. Human impacts on pine-dominated vegetation in rural landscapes in Korea and western Japan. Vegetatio. 116(2): 161-172. [79877]
42. Humphreys, M. W.; Yadav, R. S.; Cairns, A. J.; Turner, L. B.; Humphreys, J.; Skot, L. 2006. A changing climate for grassland research. New Phytologist. 169(1): 9-26. [80082]
43. Iizumi, Shigeru; Iwanami, Yuuki. 1967. Studies on the regeneration of Salix vulpina and Lespedeza bicolor after grassland fire. Bulletin of the Institute for Agricultural Research. Sendai, Japan: Tohoku University. 19: 17-23. [18731]
44. Inoue, Takenari. 2003. Chronosequential change in a butterfly community after clear-cutting of deciduous forests in a cool temperate region of central Japan. Entomological Science. 6: 151-163. [80162]
45. Iwaki, H.; Midorikawa, B. 1968. Principles for estimating root production in herbaceous perennials. In: Ghilarov, M. S.; Kovda, V. A.; Novichkova-Ivanova, L. N.; Rodin, l. E.; Sveshnikova, V. M., eds. Methods of productivity studies in root systems and rhizosphere organisms: Proceedings, International symposium of the Soviet National Committee for International Biological Sciences. 1968 August 28 - September 12; [Leningrad, USSR]. Contributions from JIBP-PT No. 21. Leningrad: Nauka: 72-78. [80164]
46. Iwanami, Yuuki. 1969. Temperatures during Miscanthus type grassland fires and their effect on the regeneration of Miscanthus sinensis. Report of the Institute for Agricultural Research. Report 330. Sendai, Japan: Tohoku University. 20: 47-88. [79974]
47. Iwanami, Yuuki. 1971. Effects of burning on regeneration of Miscanthus sinensis. Report of the Institute for Agricultural Research. Report 355. Sendai, Japan: Tohoku University. 22: 67-83. [79972]
48. Johnson, Douglas E. 1999. Surveying, mapping, and monitoring noxious weeds on rangelands. In: Sheley, Roger L.; Petroff, Janet K., eds. Biology and management of noxious rangeland weeds. Corvallis, OR: Oregon State University Press: 19-36. [35707]
49. Karp, Angela; Shield, Ian. 2008. Bioenergy from plants and the sustainable yield challenge. New Phytologist. 179(1): 15-32. [79926]
50. Kartesz, John T. 1999. A synonymized checklist and atlas with biological attributes for the vascular flora of the United States, Canada, and Greenland. 1st ed. In: Kartesz, John T.; Meacham, Christopher A. Synthesis of the North American flora (Windows Version 1.0), [CD-ROM]. Chapel Hill, NC: North Carolina Botanical Garden (Producer). In cooperation with: The Nature Conservancy; U.S. Department of Agriculture, Natural Resources Conservation Service; U.S. Department of the Interior, Fish and Wildlife Service. [36715]
51. Kashiwagi, Y. 1991. Successional development from stands of Miscanthus sinensis to stands of Pinus densiflora and elements of microclimates: the seed germination and seedling establishment conditions of P. densiflora. Theoretical and Applied Climatology. 43(3): 149-158. [80097]
52. Kayama, Masazumi. 2001. Comparison of the aluminum tolerance of Miscanthus sinensis Anderss. and Miscanthus sacchariflorus Bentham in hydroculture. International Journal of Plant Sciences. 162(5): 1025-1031. [80167]
53. Kayama, Ryosei; Yano, Norimichi; Fujimoto, Mutsuo. 1972. Studies on the relationship between Miscanthus sinensis community and soil. 4: Relationship between humus and productivity of Miscanthus sinensis grassland. Japanese Journal of Ecology. 22(5): 195-204. [80488]
54. Kayama, Ryosei; Yano, Norimichi; Sugimoto, Yoshimi. 1972. Studies on the relationship between Miscanthus sinensis community and soil. 3: Seasonal variation of production of Miscanthus sinensis grassland and the soil conditions. Japanese Journal of Ecology. 22(4): 151-161. [80486]
55. Kentucky Exotic Pest Plant Council. 2008. Invasive exotic plant list, [Online]. Southeast Exotic Pest Plant Council (Producer). Available: [2009, January 5]. [72785]
56. Kim, Chang-Hoe; Yamagishi, Satoshi; Won, Pyong-Oh. 1995. Egg-color dimorphism and breeding success in the crow tit (Paradoxornis webbiana). The Auk. 112(4): 831-839. [73148]
57. Kobayashi, Katsumi; Yokoi, Yota. 2003. Shoot population dynamics of persisting clones of Miscanthus sinensis in the warm-temperate region of Japan. Journal of Plant Research. 116(6): 443-453. [80101]
58. Kobayashi, Katsumi; Yokoi, Yota. 2003. Spatiotemporal patterns of shoots within an isolated Miscanthus sinensis patch in the warm-temperate region of Japan. Ecological Research. 18: 41-51. [80169]
59. Kobayashi, T.; Nomoto, N. 1997. Effects of trampling and vegetation removal on species diversity and micro-environment under different shade conditions. Journal of Vegetation Science. 8(6): 873-880. [79936]
60. Kowal, Norman Edward. 1966. Shifting cultivation, fire and pine forest in the Cordillera Central, Luzon, Philippines. Ecological Monographs. 36(4): 389-419. [79975]
61. Kuppinger, Dane. 2000. Management of plant invasions in the southern Appalachians. Chinquapin. 8(3): 21. [51456]
62. LANDFIRE Rapid Assessment. 2005. Reference condition modeling manual (Version 2.1), [Online]. In: LANDFIRE. Cooperative Agreement 04-CA-11132543-189. Boulder, CO: The Nature Conservancy; U.S. Department of Agriculture, Forest Service; U.S. Department of the Interior (Producers). 72 p. Available: /downloadfile.php?file=RA_Modeling_Manual_v2_1.pdf [2007, May 24]. [66741]
63. LANDFIRE Rapid Assessment. 2007. Rapid assessment reference condition models, [Online]. In: LANDFIRE. U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station, Fire Sciences Lab; U.S. Geological Survey; The Nature Conservancy (Producers). Available: /models_EW.php [2008, April 18] [66533]
64. Lane, Mike; Douglas, Joel. 1997. Evaluation of plant species for vegetative hedges. Technical Note. Coffeeville, MS: U.S. Department of Agriculture, Natural Resources Conservation Service, Jamie L. Whitten Plant Materials Center. Volume 12, No. 9. 7 p. [62976]
65. Magee, Dennis W.; Ahles, Harry E. 2007. Flora of the Northeast: A manual of the vascular flora of New England and adjacent New York. 2nd ed. Amherst, MA: University of Massachusetts Press. 1214 p. [74293]
66. Massachusetts Invasive Plant Advisory Group (MIPAG). 2005. Strategic recommendations for managing invasive plants in Massachusetts. Final report: February 28, 2005, [Online]. Massachusetts Invasive Plant Advisory Group (Producer). Available: [2009, July 2]. [71599]
67. Matsumoto, Tadao. 1971. Estimation of population productivity of Parapleurus alliaceus Germar (Orthoptera: Acridiidae) on a Miscanthus sinensis Anders. grassland. II. Population productivity in terms of dry weight. Oecologia. 7(1): 16-25. [79913]
68. McEwan, Ryan W.; Paratley, Robert D.; Muller, Robert N.; Riccardi, Cynthia L. 2005. The vascular flora of an old-growth mixed mesophytic forest in southeastern Kentucky. Journal of the Torrey Botanical Society. 132(4): 618-627. [79882]
69. McLeod, Donald Evans. 1988. Vegetation patterns, floristics, and environmental relationships in the Black and Craggy Mountains of North Carolina. Chapel Hill, NC: University of North Carolina. 222 p. Dissertation. [60570]
70. Mehrhoff, L. J.; Silander, J. A., Jr.; Leicht, S. A.; Mosher, E. S.; Tabak, N. M. 2003. IPANE: Invasive Plant Atlas of New England, [Online]. Storrs, CT: University of Connecticut, Department of Ecology and Evolutionary Biology (Producer). Available: [2010, September 27]. [70356]
71. Meyer, Mary Hockenberry; Paul, Joe; Anderson, Neil O. 2010. Competitive ability of invasive Miscanthus biotypes with aggressive switchgrass. Biological Invasions. 12(11): 3809-3816. [81153]
72. Miller, James H. 2003. Nonnative invasive plants of southern forests: A field guide for identification and control. Gen. Tech. Rep. SRS-62. Asheville, NC: U.S. Department of Agriculture, Forest Service, Southern Research Station. 93 p. Available online: [2004, December 10]. [50788]
73. Missouri Botanical Garden. 2002. Missouri exotic pest plants: A list of non-native plants that threaten Missouri's native biodiversity, [Online]. In: MO projects--North America. St. Louis, MO: Missouri Botanical Garden (Producer). Available: [2009, April 6]. [73559]
74. Mo, Wenhong; Nishimura, Noboru; Soga, Yukiko; Yamada, Kyoko; Yoneyama, Tadakatsu. 2004. Distribution of C3 and C4 plants and changes in plant and soil carbon isotope ratios with altitude in the Kirigamine grassland, Japan. Grassland Science. 50(3): 243-254. [80170]
75. Mohlenbrock, Robert H. 1986. Guide to the vascular flora of Illinois. Revised edition. Carbondale, IL: Southern Illinois University Press. 507 p. [17383]
76. Moldenke, Harold N. 1942. Noteworthy plant records and nomenclatural notes. Castanea. 7(8): 123-125. [79938]
77. Moldenke, Harold N. 1946. A contribution to our knowledge of the wild and cultivated flora of Pennsylvania--1. The American Midland Naturalist. 35(2): 289-399. [79961]
78. Mutoh, Nobuko; Kimura, Makoto; Oshima, Yasyuki; Iwaki, Hideo. 1985. Species diversity and primary productivity in Miscanthus sinensis grasslands. 1. Diversity in relation to stand structure and dominance. Botanical Magazine. 98: 159-170. [80107]
79. Nakagoshi, Nobukazu. 1984. Buried viable seed populations in forest communities on the Hiba Mountains, southwestern Japan. Journal of Science of Hiroshima University--Series B, Division 2. 19: 1-56. [80173]
80. Nakamura, Kazuo; Ito, Yosiaki; Nakamura, Masako; Matsumoto, Tadao; Hayakwa, Katsusuke. 1971. Estimation of population productivity of Parapleurus alliaceus Germar (Orthoptera: Acridiidae) on a Miscanthus sinensis Anders. grassland. 1: Estimation of population parameters. Oecologia. 7(1): 1-15. [79920]
81. NatureServe. 2011. Comprehensive report: Miscanthus sinensis--Chinese silver grass, [Online]. In: NatureServe Explorer: An online encyclopedia of life. Version 7.1. Arlington, VA: NatureServe (Producer). Available: [2011, January 19]. [81737]
82. Numata, M. 1975. Introduction: Process and results of the Japanese grassland project. In: Numata, M., ed. Ecological studies in Japanese grasslands (with special reference to the IBP area)--Productivity of terrestrial communities. JIBP (Japan International Biological Programme) Synthesis: Volume 13. Tokyo: University of Tokyo Press: 1-7. [80177]
83. Numata, Makoto. 1969. Progressive and retrogressive gradient of grassland vegetation measured by degree of succession--Ecological judgment of grassland condition and trend: IV. Vegtatio. 19(1/6): 96-127. [77129]
84. Ohtsuka, T.; Ohsawa, M. 1994. Accumulation of buried seeds and establishment of ruderal therophytic communities in disturbed habitat, central Japan. Vegetatio. 110(1): 83-96. [79935]
85. Ohtsuka, Toshiyuki; Sakura, Tsuguo; Ohsawa, Masahiko. 1993. Early herbaceous succession along a topographical gradient on forest clear-felling sites in mountainous terrain, central Japan. Ecological Research. 8(3): 329-340. [80088]
86. Racine, Charles H.; Hardin, James W. 1975. The vascular flora and vegetation in the Green River Gorge, North Carolina. Castanea. 40(4): 319-345. [72119]
87. Radford, Albert E.; Ahles, Harry E.; Bell, C. Ritchie. 1968. Manual of the vascular flora of the Carolinas. Chapel Hill, NC: The University of North Carolina Press. 1183 p. [7606]
88. Raunkiaer, C. 1934. The life forms of plants and statistical plant geography. Oxford: Clarendon Press. 632 p. [2843]
89. Rice, Elroy L. 1979. Allelopathy--an update. Botanical Review. 45(1 ): 15-109. [79891]
90. Schneider, Jennifer; Maehr, David S.; Alexy, Karen J.; Cox, John J.; Larkin, Jeffery L.; Reeder, Brian C. 2006. Food habits of reintroduced elk in southeastern Kentucky. Southeastern Naturalist. 5(3): 535-546. [75259]
91. Shindo, H; Matsui, Y.; Higashi, T. 1986. A possible source of humic acids in volcanic ash soils in Japan--charred residue of Miscanthus sinensis. Soil Science. 141(1): 84-87. [80179]
92. Shindo, Haruo. 1991. Elementary composition, humus composition, and decomposition in soil of charred grassland plants. Soil Science and Plant Nutrition. 37(4): 651-657. [80096]
93. Sorrie, Bruce A.; Gray, Janet Bracey; Crutchfield, Philip J. 2006. The vascular flora of the longleaf pine ecosystem of Fort Bragg and Weymouth Woods, North Carolina. Castanea. 71(2): 129-161. [71947]
94. South Carolina Exotic Pest Plant Council. 2008. Invasive plant list, [Online]. Nashville, TN: Southeast Exotic Pest Plant Council (Producer). Available: [2009, January 5]. [72717]
95. Steury, Brent W; Davis, Charles A. 2003. The vascular flora of Piscataway and Fort Washington National Parks, Prince Georges and Charles Counties, Maryland. Castanea. 68(4): 271-299. [73054]
96. Stewart, J. Ryan; Toma, Yo; Fernandez, Fabian G.; Nishiwaki, Aya; Yamada, Toshihiko; Bollero, German. 2009. The ecology and agronomy of Miscanthus sinensis, a species important to bioenergy crop development, in its native range in Japan: a review. GCB Bioenergy. 1: 126-153. [80136]
97. Stickney, Peter F. 1989. Seral origin of species comprising secondary plant succession in Northern Rocky Mountain forests. FEIS workshop: Postfire regeneration. Unpublished draft on file at: U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station, Fire Sciences Laboratory, Missoula, MT. 10 p. [20090]
98. Strausbaugh, P. D.; Core, Earl L. 1977. Flora of West Virginia. 2nd ed. Morgantown, WV: Seneca Books. 1079 p. [23213]
99. Swearingen, J.; Reshetiloff, K.; Slattery, B.; Zwicker, S. 2002. Plant invaders of mid-Atlantic natural areas. [Washington, DC]: U.S. Department of the Interior, National Park Service; Fish and Wildlife Service. 82 p. Available online: [2009, November 19]. [54192]
100. Takeuchi, Keita; Shimano, Koji. 2009. Vegetation succession at the abandoned Ogushi sulfur mine, central Japan. Landscape and Ecological Engineering. 5(1): 33-44. [80079]
101. Tallamy, Douglas W. 2004. Do alien plants reduce insect biomass? Conservation Biology. 18(6): 1689-1692. [50870]
102. Tang, Yan-Hong; Washitani, Izumi; Tsuchiya, Takayoshi; Iwaki, Hideo. 1988. Fluctuation of photosynthetic photon flux density within a Miscanthus sinensis canopy. Journal of Ecology. 3: 253-266. [80089]
103. Tang, Yanhong; Washitani, Izumi; Iwaki, Hideo. 1992. Seasonal variations of microsite light availablity within a Miscanthus sinensis canopy. Ecological Research. 7(2): 97-106. [80094]
104. Tennessee Exotic Pest Plant Council. 2001. Tennessee invasive exotic plant list, [Online]. In: Invasive exotic plants in Tennessee. Fairview, TN: Tennessee Exotic Pest Plant Council (Producer) Available: [2009, June 12]. [74677]
105. Toyohara, Gentaro; Fujihara, Michiro. 1998. Succession of secondary forests affected by pine wilt disease in western Japan followed on vegetation maps. Applied Vegetation Science. 1(2): 259-266. [79940]
106. Tsuyuzaki, Shiro. 2005. Miscanthus sinensis grassland is an indicator plant community to predict forest regeneration and development on ski slopes in Japan. Ecological Indicators. 5(2): 109-115. [80113]
107. Tucker, G. E. 1972. The vascular flora of Bluff Mountain, Ashe County, North Carolina. Castanea. 37(1): 2-26. [73963]
108. U.S. Department of Agriculture, Natural Resources Conservation Service. 2011. PLANTS Database, [Online]. Available: /. [34262]
109. U.S. Department of the Interior, Fish and Wildlife Service, Division of Endangered Species. 2011. Threatened and endangered animals and plants, [Online]. Available: [62042]
110. Uesaka, Shohei; Tsuyuzaki, Shiro. 2004. Differential establishment and survival of species in deciduous and evergreen shrub patches and on bare ground, Mt. Koma, Hokkaido, Japan. Plant Ecology. 175(2): 165-177. [79932]
111. Watanabe, Nariyasu; Nishiwaki, Aya; Sugawara, Kazuo. 2001. Seed banks in pastures: special reference to a persistent soil seed bank of invading species Carex albata Boott. Grassland Science. 47(4): 337-343. [80182]
112. Weatherbee, Pamela B.; Somers, Paul; Simmons, Tim. 1998. A guide to invasive plants in Massachusetts. Westborough, MA: Massachusetts Division of Fisheries and Wildlife. 23 p. [71448]
113. Werger, Marinus J. A.; Hirose, Tadaki; During, Heinjo J.; Heil, Gerrit W.; Hikosaka, Kouki; Ito, Takehiko; Nachinshonhor, U. G.; Nagamatsu, Dai; Shibasaki, Katsuhiko; Takatsuki, Seiki; van Rheenen, Jan W.; Anten, Niels P. R. 2002. Light partitioning among species and species replacement in early successional grasslands. Journal of Vegetation Science. 13(5): 615-626. [75817]
114. White, Deborah L.; Drozda, Nicholas C. 2006. Status of Solidago albopilosa Braun (white-haired goldenrod) [Asteraceae], a Kentucky endemic. Castanea. 71(2): 124-128. [79880]
115. White, Rickie D., Jr. 2003. Vascular plant inventory and plant community classification for Carl Sandberg Home National Historic Site. NatureServe Technical Report: Prepared for the National Park Service under Cooperative Agreement H 5028 01 0435. Durham, NC: NatureServe. 152 p. [79627]
116. Wofford, B. Eugene. 1989. Guide to the vascular plants of the Blue Ridge. Athens, GA: The University of Georgia Press. 384 p. [12908]
117. Wunderlin, Richard P.; Hansen, Bruce F. 2003. Guide to the vascular plants of Florida. 2nd ed. Gainesville, FL: The University of Florida Press. 787 p. [69433]
118. Yamane, Ichiro; Ito, Iwao; Sato, Katsunobu; Kumada, Denzaburo. 1958. On the relationship between vegetation and soil at mountain grassland in northeastern Japan. Part 3. Growing process and inorganic and organic constituents of predominant plant species and some characteristics of soil. Report of the Institute for Agricultural Research. Report 330. Sendai, Japan: Tohoku University. 9: 1-43. [80183]

FEIS Home Page