Polygonum sachalinense

Distribution: Giant knotweed has a discontinuous distribution in North America. In eastern North America, giant knotweed occurs from Tennessee and North Carolina north into eastern Canada. Some states in the Great Lakes region (e.g., Indiana) and New England (e.g., New Hampshire) lack giant knotweed. Giant knotweed is also found in Louisiana. In western North America, giant knotweed occurs from California north to Alaska, with populations also in Idaho and Montana.

Japanese knotweed is more widely distributed than giant knotweed. The Plants Database reports Japanese knotweed occurring in almost all of the United States with the exceptions of Florida, Alabama, Texas, New Mexico, Arizona, Wyoming, and North Dakota. However, one source documented Japanese knotweed in Arizona [39]. Japanese knotweed occurs throughout Canada, with the exceptions of Labrador, Saskatchewan, Alberta, Northwest Territories, and Yukon. Plants Database provides distribution maps of giant and Japanese knotweed.

As of this writing (2010), the distribution of Bohemian knotweed in North America is not well known. The Plants Database reports Bohemian knotweed occurring in British Columbia, Ontario, and Quebec (2010). However, sources included in this profile have also documented Bohemian knotweed in New York [97,107] and Washington [31,109,111,153]. It is likely that the distribution of all 3 knotweeds is expanding in the United States.

Introduction to North America: Both giant [49,85,98,121] and Japanese [46,98] knotweed are native to Asia. During the late 19th century, giant [42] and Japanese [98] knotweed were introduced to North America as ornamental plants. Giant knotweed was also promoted as a soil binder [42] and fodder plant [136]. One source reports Japanese knotweed established from seeds released from ship ballast in New York [6]. Giant [98] and Japanese knotweed [6,49,51,85,142,146] escaped cultivation, with herbarium records indicating that Japanese knotweed escaped cultivation at least 115 times in North America prior to 2003 [6].

Rate of spread: There is some information available regarding the rate of spread of Japanese knotweed, though as of this writing (2010) information was limited for Bohemian knotweed and lacking for giant knotweed. After initial introductions, Japanese knotweed populations displayed a 50-year lag time prior to exponential population growth. As of 2006, spread rates in the United States were increasing rapidly, while those in Canada leveled off in the 1970s [6]. In Washington, Japanese knotweed was established in one county in 1960; by 2000, it was established in more than 50 counties [127]. Along the Hoh River in northwestern Washington, one Bohemian knotweed plant was transported downstream in a winter storm event. Approximately 4 years after this event, 9,600 stems were located within 20 river miles of where this plant established. Five years after the flooding event, 18,585 stems were mapped within the same 20 river miles [111].

Means of spread: The spread of all 3 knotweeds is linked to the ability of both aboveground and belowground parts to sprout when separated from the parent plant (see Vegetative regeneration). Humans spread the plants through dumping yard waste [31,40], roadside mowing or construction projects [40], or using fill dirt from riparian areas [8]. Plants of all 3 knotweeds that escape cultivation and establish in riparian areas may spread when plant parts are transported downstream ([2,93,112,136], review by [7]). Spread by seed is rare, though it has been suggested for Japanese knotweed [141,151], and seedlings of giant [87], Japanese [16,44,74], and Bohemian [115] knotweed have been observed.

Reynoutria sachalinensis (F. Schmidt) Nakai:
South Africa (Africa & Madagascar)

Note: This information is based on publications available through Tropicos and may not represent the entire distribution. Tropicos does not categorize distributions as native or non-native.

Polygonum sachalinense F. Schmidt:
Canada (North America)
United States (North America)

Note: This information is based on publications available through Tropicos and may not represent the entire distribution. Tropicos does not categorize distributions as native or non-native.

introduced; B.C., N.B., Nfld. and Labr. (Nfld.), N.S., Ont., P.E.I., Que.; Calif., Conn., Del., Idaho, Ill., Ky., La., Maine, Md., Mass., Mich., Mont., N.J., N.Y., N.C., Ohio, Oreg., Pa., R.I., Tenn., Vt., Va., Wash., W.Va., Wis.; Asia (Japan); introduced in Europe.

Canada

Origin: Exotic

Regularity: Regularly occurring

Currently: Unknown/Undetermined

Confidence: Confident

United States

Origin: Exotic

Regularity: Regularly occurring

Currently: Unknown/Undetermined

Confidence: Confident

Far East (southern Sakhalin, southern Kuril Islands) and northern Japan. Along streams, on gravelly and sandy soil, among shrubs. Also creates a tall-herb formation.

More info for the terms: adventitious, geophyte

Botanical description: This description covers characteristics that may be relevant to fire ecology and is not meant for identification. Keys for identification of giant and Japanese knotweed are available (e.g., [49,58,78,85,98,142]). For information on differentiating between giant, Japanese, and Bohemian knotweed, see the following: [7,43,153]. These 3 knotweeds are commonly confused [7,16,43,153].

Giant knotweed is a stout, rhizomatous, perennial geophyte (review by [7]). Observations from the Czech Republic suggest that giant knotweed roots grow "deep" into the soil. Rhizomes have a diameter of 3 inches (8 cm) and may spread 50 to 65 feet (15-20 m) laterally [79]. Giant knotweed stems are generally clustered, erect [42], hollow, and up to 13 feet (4 m) tall. Leaves are alternate, oval to oblong, and large, frequently 12 inches (30 cm) long, with a cordate base [121]. Flowers are white [94] or greenish and borne on axial or terminal racemes or panicles. Seeds are triangular achenes [121] with 3-mm long nutlets [94].

Giant knotweed flowers.

Japanese knotweed is a stout, rhizomatous, perennial geophyte. Rhizomes are dark brown, knotty, up to 3 inches (8 cm) in diameter (review by [7]), and may spread laterally 23 to 65 feet (7-20 m) [115]. Japanese knotweed has a deep central taproot (reviews by [7,11]). Adventitious roots are white, fine, and thread-like. Stems are 3 to 13 feet (1-4 m) tall, glaucous, erect, and hollow (review by [7]). Japanese knotweed plants are often shrubby or woody at the base [98]. Leaves are alternate and broadly ovate (3 to 6 inches (8-15 cm) by 2 to 5 inches (5-12 cm)) with a truncate base [94]. Flowers are borne on axial or terminal racemes or panicles 3 to 6 inches (8-15 cm) long. Flowers are creamy-white. Seeds are tri-winged achenes (review by [7]).

Bohemian knotweed exhibits botanical characteristics similar to those of giant and Japanese knotweed, though it is intermediate in leaf size ([153], review by [7]).

• Botanical description
• RAUNKIAER LIFE FORM

Herbs, perennial, rhizomatous, 2-4(-5) m. Stems usually clustered, erect, sparingly branched, herba-ceous, stiff, glabrous, glaucous. Leaves: ocrea persistent or deciduous, brownish, cylindric, 6-12 mm, margins oblique, face without reflexed and slender bristles at base, otherwise glabrous or puberulent; petiole 1-4 cm, glabrous; blade ovate-oblong, 15-30(-40) × 7-25 cm, base cordate, margins entire, glabrous or scabrous to ciliate, apex obtuse to acute, abaxial face minutely dotted, glaucous, with hairs along veins distinctly multicellular, 0.2-0.6 mm, tips acute to acuminate, adaxial face glabrous. Inflorescences axillary, mostly distal, erect or spreading, paniclelike, 3-8 cm, axes puberulent to pubescent; peduncle 0.1-4 cm or absent, puberulent to reddish-pubescent. Pedicels ascending or spreading, articulated proximal to middle, 2-4 mm, glabrous. Flowers bisexual or pistillate, 4-7 per ocreate fascicle; perianth accrescent in fruit, greenish, 4.5-6.5 mm including stipelike base, glabrous; tepals obovate to elliptic, apex obtuse to acute, outer 3 winged; stamens 6-8; filaments flattened proximally, glabrous; styles connate basally; stigmas fimbriate. Achenes included, brown, 2.8-4.5 × 1.1-1.8 mm, shiny, smooth; fruiting perianth glabrous, wings flat to undulate, 1.8-2.2 mm wide at maturity, decurrent on stipelike base to articulation, margins entire. 2n = 44, 66, 102, 132 (Japan, Korea).

Stems 1.5-3 (-4) m. Unbranched or sparsely branched. Rhizome creeping, horizontal, deep-lying (70-100 cm below soil surface). One plant can cover an area of 30 square meters. Leaves shortly petiolate, oblong, 20-40 cm x 10-20 cm. Inflorescence short, axillary, flowers white. V - mid spring to late autumn. Fl - July for one month. Fr - September, not every year. Propagated by division (runners) and seed. Grows in full sun and also in partial shade. Creates a herbaceous thicket and can grow in sites of low maintenance. Z 4.

Polygonum sachalinense F. Schmidt, Mém. Acad. Imp. St.-Pétersbourg Divers Savans 9: 233. 1859; Reynoutria sachalinensis (F. Schmidt) Nakai; Tiniaria sachalinensis (F. Schmidt) Janchen

More info for the terms: avoidance, rhizome

Site description: Giant knotweed establishes in disturbed areas [42,78], including railroads [142], roadsides [78,142], and old homesites [142]. In Pennsylvania, giant knotweed established on abandoned fill and gravel and sand roadway materials [87]. A field guide reported that giant knotweed is likely to establish along streams or streambanks and in forests or woodlands of the Upper Midwest [28].

Japanese knotweed commonly establishes in disturbed areas ([53,65,78,83,98,114], review by [102]), including roadsides [8,32,40,51,56,73,78,98,114,142], along railroad tracks [6,56,74], in gravel pits, dumps [142], vacant lots [56,83], pastures [56], and abandoned fields [83] or gardens [51,56,83]. Japanese knotweed also occurs in woodland thickets [56] and borders [9], edge habitats [41], ravines [65], early successional forests, wetlands, wet meadows [83], floodplain forests [83,114], and the margins of ponds and lakes [114]. One source reports Japanese knotweed spreading from roadsides into adjacent forests in New York [73].

Descriptions of characteristics of sites with Bohemian knotweed are lacking in the literature (2010). One source reports it escaping cultivation and establishing on riverbanks, roadsides, garden dumps, and disturbed ground in western Washington [153].

Elevation: There is little information regarding the elevational limits of the 3 knotweeds in North America (2010). One flora reports that giant knotweed occurs from 0 to 1,800 feet (0-550 m) in North America [42]. Japanese knotweed was reported from 4,000 to 6,000 feet (1,220-1,830 m) in Utah [147] and at "low" elevations in Colorado [146]. In Japan, the upper elevation limit of Japanese knotweed is approximately 8,200 feet (2,500 m), with seedling survival decreasing as elevation increases [80].

Climate: The 3 knotweeds encounter a variety of climates throughout their North American distribution. In Washington where all 3 knotweeds occur, the average monthly maximum and minimum temperatures are 60 °F (15 °C) (August) and 40 °F (5 °C) (January). Annual precipitation averages 72 inches (1,820 mm), of which 27 inches (680 mm) falls as snow [136]. In the United States, Japanese knotweed appears to be established in all areas with more than 20 inches (>500 mm) mean annual precipitation (review by [102]).

Several sources suggest that the 3 knotweeds are limited by climate or weather events ([74,87], reviews by [7,11]). Aboveground shoots are highly susceptible to both late spring and early autumn frosts, which cause leaf drop, while the rhizome systems are able to survive in frozen soils. Early spring frosts often cause dieback, followed by regeneration from rhizomes (review by [7]). Short growing seasons and frosts that damage rhizomes also limit the ability of Japanese knotweed plants to store reserves for winter survival (review by [11]). However, one source reports that Japanese knotweed rhizome fragments dug from the ground and left out over winter were still able to regenerate [25]. At field experiment sites in Pennsylvania, giant knotweed seedlings not protected by experimental light barriers experienced early frost damage, while those under light barriers grew into October [87]. In Japan, Japanese knotweed seedlings with a dry weight of <10 mg were unable to survive a winter at either 4,600 feet (1,400 m) or 8,200 feet (2,500 m); seedlings exhibited 100% overwinter survival when dry weight was ≥40 mg. Survival was higher at 4,600 feet (1,400 m) where growing seasons were longer and winter temperatures were higher than at 8,200 feet (2,500 m) [80]. In the United Kingdom, Japanese knotweed plants were vulnerable to spring winds that damaged undeveloped leaves (review by [11]).

Some sources predict an expansion in the range of Japanese knotweed in Europe with the increasing temperatures expected from global climate change (review by [7]). Reports of recent high seed production by the 3 knotweeds in Europe could be partially due to warmer climate; as a late-season flowerer, seed production is reportedly limited by early-season frosts [3]. For information on how climate change might increase the invasiveness of Japanese knotweed in the United Kingdom see [10].

In North America, results from a Massachusetts study suggest that warming climates may allow additional Japanese knotweed seedling survival in places where cold temperatures currently limit survival. However, shade was found to be more limiting to seedling survival than climate in this study [44].

Soils: Japanese (reviews by [11,102]) and giant knotweed (review by [118]) are not limited by soil type. In its native range, Japanese knotweed commonly occurs on basaltic gravels [80]. In New Jersey, Japanese knotweed was found on sites with a range of soil textures, including silt, silt loam, and beach sand [74]. In the central Cascades of Washington, Japanese knotweed established on gravelly sandy loam [40]. Near Washington, DC, Japanese knotweed occurred on sandy loam, sand, and loamy sand [104].

Little information is available on soil nutrient preferences of the 3 knotweeds (2010). Japanese knotweed tolerated a range of soil nutrient levels in New Jersey [74]. In United Kingdom, Japanese knotweed established on relatively nutrient-rich soils (review by [11]).

Japanese knotweed can tolerate low soil pH; it is not clear if this pattern applies to giant or Bohemian knotweed. A guide for revegetating minespoils reports that Japanese knotweed tolerates extremely acidic soil, with a lower pH limit of 3.5 [141]. It grew in a range of soil pH in New Jersey (4.5 to 7.4) and was not limited by pH in the United Kingdom (review by [11]). Japanese knotweed had high survival (80%) 4 growing seasons after planting on acid surface-mine spoils in eastern Kentucky [91]. The Russian Agricultural Ministry suggests the avoidance of acidic soils when planting giant knotweed (review by [118]).

On Long Island, New York, Japanese and Bohemian knotweed have established in salt marshes. Greenhouse experiments demonstrated that individual plants varied in their response to different levels of salt exposure, suggesting that salt tolerance is not genetically predetermined but is determined by exposure [97]. In New Jersey it was noted that Japanese knotweed tolerated salt spray from the ocean [74].

The prevalence of the 3 knotweeds in riparian areas suggests tolerance of high soil moisture. Most herbarium specimens from North America documented Japanese knotweed in locations with high soil moisture (review by [7]). In New Jersey, Japanese knotweed often established near streams where soils were likely saturated with water through a majority of the growing season [74]. In New York, Japanese knotweed occurred on both dry and moist ruderal sites [35]. The occurrence of Japanese knotweed on dry ruderal sites suggests an ability to tolerate low soil moisture, though one study attributed slow seedling growth to dry local conditions [44]. The Russian Agricultural Ministry suggested avoiding excessively damp soils when planting giant knotweed (review by [118]). In the Czech Republic, it was reported that giant knotweed prefers sites with plenty of water [79].

Disturbed places; 0-500m.

In Great Britain and/or Ireland:
Foodplant / saprobe
scattered, subepidermal, piercing pycnidium of Amphorula coelomycetous anamorph of Amphorula sachalinensis is saprobic on dead stem of Fallopia sachalinensis

Foodplant / saprobe
sclerotium-like pycnidium of Chaetoconis coelomycetous anamorph of Ceriospora polygonacearum is saprobic on dead stem of Fallopia sachalinensis
Remarks: season: 3-4

Foodplant / saprobe
immersed, loosely gregarious pycnidium of Phomopsis coelomycetous anamorph of Phomopsis polygonorum is saprobic on dead, epidermis blackened stem of Fallopia sachalinensis
Remarks: season: 5-8

More info for the term: fire regime

It is not known what type of fire regime the 3 knotweeds are best adapted to. They are common in riparian areas in many parts of North America, and FIRE REGIMES in riparian areas are often related to the FIRE REGIMES of adjacent upland communities. Thus FIRE REGIMES for plant communities with the 3 knotweeds could be quite variable. See the Fire Regime Table for further information on FIRE REGIMES of vegetation communities in which the 3 knotweeds may occur.

More info for the terms: cover, fuel, fuel loading, litter, tree

It is not clear whether occurrence of the 3 knotweeds changes the fuel characteristics of invaded plant communities. Fuel characteristics of plant communities could potentially be altered in areas where the 3 knotweeds exhibit fuels traits (e.g., flammability, fuel loading, plant architecture), densities, and/or growth patterns differing from those of native vegetation.

Laboratory analyses suggest that Japanese knotweed foliage and stems are not particularly flammable [33]. Giant knotweed appears to exhibit similar characteristics. In the Czech Republic, the water content of spring giant knotweed stems reached values as high as 1,800% of dry mass. After 2 months, stem water content decreased and matched that of leaves, at 400% of dry mass [79]. In Russia, giant knotweed stems and leaves reportedly had an 82% moisture content. Consequently, Russian forestry officials investigated the use of 7-foot-tall stands of giant knotweed (referred to as Sakhalin buckwheat) as a live fire break to protect tree plantations. The testing occurred on a hot, dry day with a mild south wind. "The reaction of Sakhalin buckwheat thicket to forest fire was tested by igniting a brush fire in the wind direction 7 feet from the thicket edge. The incendiary fuel was brushwood, pine branches, drenched copiously with kerosene. Set ablaze on the buckwheat thicket side of the plantation, the brush fire whipped by wind burned fiercely for 30 minutes. The test established that buckwheat thickets minimize the effect of fire and at 8-inch depth localize it. The fire does not spread across the thicket to the tree plantation growing on the other side of the protective green zone. The zone itself suffers little from the effect of fire. Only 10% of the foliage embraced in flames, was curled up from burning. The thicket continued to stand upright. The commission concluded that thickets of Sakhalin buckwheat are a completely effective barrier against low forest fires and can be recommended for planting in fireproof zones and banks" (Russian Agricultural Ministry cited in [118]).

As of this writing (2010) no studies have documented fuel characteristics of litter of the 3 knotweeds. Litter accumulations can be high in some stands. In old fields in south-central New York, litter depth was higher in Japanese knotweed stands compared to outside the stands, though the litter material was almost all large, fibrous stems (P<0.05) [77]. In Pennsylvania it was noted that dense litter built up every autumn under riparian stands composed of all 3 knotweeds, though litter was generally washed away by summer [87]. In riparian forests of northwestern Washington, total mass of autumn litterfall did not differ between plots with and without established giant knotweed, though litter composition varied [136].

Occurrence of the 3 knotweeds may result in changes in aboveground vegetative structure that could impact fuel characteristics. Changes in vegetative architecture were observed in old fields in south-central New York. Vegetation height increased abruptly at the edge of Japanese knotweed stands, and average height of the first leaf was higher in Japanese knotweed stands compared to outside of stands [77]. In Belgium, plots with Japanese knotweed had higher aboveground biomass compared to plots with native vegetation (2.95 vs. 0.56 kg/m²) [29,30]. The 3 knotweeds often cover extensive areas [31,44,53,61,103,107,116,125] and may dominate local vegetation ([73,87], review by [118]) (see Plant growth).

• Fuels
• FIRE REGIMES

More info on this topic.

More info for the terms: cover, natural, presence

The presence of giant [42,78,115], Japanese ([12,53,65,73,78,83,98,114,115], reviews by [11,88,102]), and Bohemian [115,153] knotweed in disturbed areas suggests a preference for early-successional sites. In their native ranges, giant [131] and Japanese ([131], review by [7]) knotweed are early-successional species, often among the first species to colonize recent lava flows. In the Pacific Northwest, all 3 knotweeds commonly established on freshly disturbed soils, like floodplains and cobble bars, following flooding [115]. One review listed plant communities where Japanese knotweed could establish in mountainous ecoregions of the northwestern United States. In all cases, disturbance was listed as a requirement for establishment [88]. Another review stated that Japanese knotweed is promoted by soil disturbance and high light environments in the southern United States; it does not appear to establish in undisturbed sites or forest interiors, though it may be able to establish in canopy gaps created by natural or human-made disturbance [38].

Some evidence suggests that giant [136] and Japanese ([19,81,103], reviews by [11,38,102]) knotweed grow better with more light. In Massachusetts, Japanese knotweed grew in full sun to full shade, but was considered "hardier" in full sun [81]. In growth chamber experiments, Japanese knotweed plants in high light had greater leaf area (P<0.05) and belowground biomass (P<0.001) than those in low light [103]. Two-year-old Japanese knotweed rhizomes planted on streambanks near Washington, DC, exhibited significantly higher survivorship (P<0.05) and greater stem growth (P<0.001), basal stem diameter (P<0.001), and stem height (P<0.01) than rhizomes planted in a forest understory. Streambank sites had significantly higher light levels than understory sites (P<0.01) [103]. Managers treating Japanese knotweed in southwestern Washington found smaller stems and plants in deeply shaded areas compared to more open areas [19]. Results from both field (full and 50% sun) and growth chamber (high and low light) experiments in North Carolina documented that giant knotweed plants grown in high-light conditions had higher photosynthetic rates than those grown in low-light conditions (P<0.05) [89].

Despite these findings, all 3 knotweeds have been documented growing in shady understories. One review reports giant knotweed growing well in semi-shaded places and along the edges of forests [118]. In northwestern Washington giant knotweed was found in low terrace and floodplain forests with an average canopy cover of 47.2% (range 2.5% to 85.0%) [136]. In Nova Scotia, Japanese knotweed did not appear to spread from shaded into open areas [98]. Along the Hoh River in northwestern Washington, Bohemian knotweed was found to grow slowly but persistently in the complete shade of red alder or willow, as well as under a dense, coniferous canopy [111].

Successional role: Changes in native plant cover or species richness in areas where the 3 knotweeds have established [13,48,57,77,136] suggest they could alter the successional trajectories of native plant communities (see Impacts). Some sources identify Japanese knotweed as a nursery plant in early successional communities, particularly in its native range, because it facilitates soil development and the establishment of later successional species (review by [7]).

More info for the terms: cover, density

Plant growth: Japanese knotweed exhibits rapid growth [98]. Over the New Jersey growing season of approximately 80 days, the average rate of Japanese knotweed growth was 3.28 inches (8.35 cm)/day [74]. In the Pacific Northwest, Japanese knotweed stems reached 10 feet (3 m) by June [115]. Giant knotweed also exhibits fast growth [136]. In the Czech Republic, early spring giant knotweed shoots grew an average of 1 inch (3 cm)/day for 20 days, then increased growth to approximately 2 inches (5 cm)/day [79]. In the Pacific Northwest, giant knotweed stems reached 15 feet (4.5 m) by June [115]. Several sources report that Japanese knotweed grows better in full sun than partial shade ([19,81,103], reviews by [11,38,102]). See Successional status for more information on this topic.

Populations of one or more of these 3 knotweeds may cover extensive areas. In Washington, DC, 2 streamside stands of Japanese knotweed extended 282 feet (86 m) and 190 feet (58 m), respectively [103]. Approximately 25% of individual Japanese and Bohemian knotweed plants surveyed in Belgium covered >0.02 acres (100 m²) [125].

Maximum stand size reported for 3 knotweed taxa Species Location Stand size (acres) Bohemian Washington 16 [31] New York 0.6 [107] Japanese Massachusetts 0.006 [44] >0.02 [53] All 3 Oregon 1 [116]

In the United Kingdom, one Japanese knotweed plant occupied approximately 245 acres (100 ha) (S. Hatherway personal communication cited in [61]). This extensive growth plus the identification of all Japanese knotweed plants in the United Kingdom as genetically identical suggests that it might be one of the largest vascular plants on earth [61], prompting the newspaper headline: "Largest female on earth could strangle Britain" (review by [4]).

These 3 knotweeds grow in dense stands and often become the dominant vegetation ([73,87], review by [118]). Two- to 3-year-old giant knotweed plantings produced enough "root runners" that no vegetation of any kind could grow under their mat (review by [118]). Japanese knotweed stands in Colorado were characterized as "dense thickets of rank growth" [146]. In New York, vegetative cover of roadside Japanese knotweed was 81.3% in study plots with a total plant cover of 84.6% [73]. In Michigan, Japanese knotweed established in dense thickets >7 feet (2 m) tall [142]. In southwestern Washington, managers treated over 300,000 Japanese knotweed stems in 500 acres (200 ha) of treatments [19]. In northwestern Washington, giant knotweed stem density in low terrace and floodplain forests ranged from 0.0 to 8.8 stems/m² [136].

More info for the terms: cover, litter, presence

Documentation of seedlings of the 3 knotweeds is rare, and parentage of seedlings is often unclear [148]. Several sources report that seedling survivorship is poor in the field ([44,74,87], review by [102]), though there is the potential for seedlings to establish given the right conditions [44]. Light [44,74], moisture [44], litter levels [87], weather [44,80], and the presence of established vegetation [44,87,141,151] may all impact seedling survivorship.

At field sites in New Jersey, Japanese knotweed seedlings that germinated under the canopy of a parent plant rapidly declined in number after reaching the 3-leaf stage. No seedlings survived in the wild over 5 years of observation though early-season seedling densities were as high as 486 seedlings/0.5 m². In shading experiments, planted Japanese knotweed seedlings subjected to high light levels grew vigorously, stems were well-branched, and leaves were large, rich, and dark green. Seedlings grown at low light levels lacked vigor by the second week of the study. These seedlings had low growth and branching rates as well as small leaves that showed signs of chlorosis [74].

Observations from a second study suggest that both light and moisture may affect Japanese knotweed seedling survival. In Massachusetts, Japanese knotweed seedlings were observed at several field locations. At one site, seeds germinated but seedlings died after 1 month, which the authors attributed to the dense cover of Japanese knotweed sprouting from established rhizomes. At another site, seeds germinated but seedling growth was slow, which the authors attributed to dry local conditions. The seedlings ultimately died after the area was disturbed during a construction project. At another site, hundreds of seedlings emerged in an area lacking Japanese knotweed after a flowering stem from an uphill plant collapsed downslope. Despite shading from other plants, seedlings grew and developed through the season, with some individuals gaining as many as 5 true leaves. Though frost killed aboveground vegetation, surviving seedlings developed rhizomes in their first year. Few seedlings survived to the next year. The authors concluded that seedlings emerging underneath well-established stands of Japanese knotweed are not likely to survive because the rapid growth of vegetation from the rhizomes creates a canopy in early spring that blocks most sunlight. However, seedlings emerging in open areas have the potential to survive through the next growing season and establish successfully [44].

In Pennsylvania, tens of thousands of newly germinated seedlings were observed in populations with all 3 knotweeds. Differences in seedling survival were related to the proximity to mature plants; those seedlings that germinated under the canopy of parent plants and in the leaf litter did not survive. Thousands of seedlings did survive to the end of the first growing season, some reaching heights of >4 inches (10 cm). Second-year seedlings of giant knotweed were observed at some locations, with completely independent root systems and remnant stems from previous growth. In field experiments, giant knotweed seeds were planted and exposed to various treatments, including 3 shade levels (0%, 30%, and 63%), 2 leaf litter conditions (absent, present), and 2 seed sources. Litter had a significant negative impact on seedling biomass (P=0.05) while shade level did not. The author suggested that litter both physically prevented seedlings from reaching light and provided a habitat for slugs that ate the seedlings. The author also noted that seedlings not protected by shade experienced early frost damage, while those under shade grew into October [87].

In Japan, the ability of Japanese knotweed seedlings to survive overwintering is related to winter temperature and seedling size. One study compared seedling survival at elevations of 4,600 feet (1,400 m) or 8,200 feet (2,500 m). Japanese knotweed seedlings with a dry weight of <10 mg were unable to survive winter at either elevation, but 100% of seedlings with a dry weight of ≥40 mg survived. Seedling survival was higher at the lower elevation, a pattern attributed to the relatively long growing season and high winter temperatures at low elevations [80].

A guide for revegetating minespoils in the eastern United States reported that Japanese knotweed "spreads by seeds into gullies and over considerable distances on barren areas. However, it does not readily spread by seed into stands of established vegetation" [141]. Japanese knotweed reportedly spread by seed across minespoil sites in Pennsylvania. The highest number of seedlings was found under the cover of adult Japanese knotweed plants compared to areas where other plants were either established or had been planted. The authors concluded that high herbaceous plant and grass cover prevented Japanese knotweed seedling establishment [151].

More info for the terms: cover, litter, series

Seeds collected from all 3 knotweeds in North America have germinated in laboratory settings [44,46,74,87]. Germination in nonexperimental settings is rare though it has been documented for giant [87], Japanese [16,44,74], and Bohemian [115] knotweed as evidenced by seedlings. The germination potential of seeds from the 3 knotweeds likely varies with characteristics (e.g., breeding system) of the population studied. Not all North American populations produce fertile seeds [74,87,115]. Pollen sources of studied populations are often unknown; one review reports that the seed source for several North American germination experiments could be any of the 3 knotweeds [148]. Consequently, the results of germination studies should be interpreted with caution and broad inferences may not be possible. The following information retains the names of knotweed taxa used by the authors.

Giant knotweed: Laboratory experiments in Massachusetts found that giant knotweed seeds took 16 to 37 days to germinate [46]. Giant knotweed seed germination is favored by moisture ([129], review by [118]) and disturbance [87,129]. In its native Japan, giant knotweed seed germination was high within rills in heavily eroded areas on volcanic deposits. Water content within the rills seemed to promote germination [129]. In Pennsylvania, thousands of giant knotweed seedlings emerged in areas disturbed by earth-moving equipment the previous year [87]. The Russian Agricultural Ministry suggested avoiding acidic soils, excessively damp soils, and loose sands when planting giant knotweed. It was recommended that seeds be moistened prior to planting (review by [118]).

Light may not influence giant knotweed germination, though only 1 study has addressed this topic as of 2010. In Pennsylvania, giant knotweed seeds were planted in fields under various experimental conditions, including 3 shade levels (0%, 30%, and 63%), 2 leaf litter conditions (absent, present), and 2 seed sources. Giant knotweed seeds germinated from all treatments. Sites with litter had lower germination than sites without litter across all 3 shade treatments (P=0.05). Low light availability did not result in decreased germination [87].

Japanese knotweed: Laboratory experiments in Massachusetts found that Japanese knotweed seeds took 5 to 55 days to germinate [46]. Laboratory germination of wild-collected Japanese knotweed seeds from New Jersey was not influenced by light, temperature, or moisture during storage. Pin-prick scarification tests suggested that scarification hindered germination. Germination was positively associated with cold treatment and negatively associated with storage period (P=0.01) [74].

Greenhouse experiments and field observations in Massachusetts suggest that Japanese knotweed germination may be high though seedling survival is limited. In a greenhouse, germination of wild-collected Japanese knotweed seed was highly variable, though some samples achieved 100% germination. Seeds did not require burial to germinate; those on the soil surface germinated several days before those that were buried 0.2 inches (0.5 cm). Seeds germinated after exposure to simulated New England weather conditions, though seedlings did not survive [44]. See Seedling establishment and growth for information on field germination and seedling survival from this study.

A series of field studies was conducted in Pennsylvania to assess the potential for Japanese knotweed to germinate under field conditions. In one experiment, Japanese knotweed seeds were collected in late October, dried, and planted in bags in late December in existing stands of Japanese knotweed. The bags were excavated in March and every 3 weeks afterward and the germinated seeds were counted. Germination rates ranged from 55% to 92% and averaged 82%. Roughly 30% of the seeds germinated before March 10, but germination date varied by location. In a second experiment, seeds that had overwintered were collected from stems in March. Seeds were planted in different microhabitats, including areas without previous Japanese knotweed establishment. Emerging seedlings were counted from April to August. Seeds germinated at several sites, including both riparian and wooded upland areas, though there was no way to identify if the emerging seedlings originated from the planted seeds or from the naturally occurring seed bank. Peak number of seedlings varied between microhabitats, and was greatest in plots in areas with established Japanese knotweed stands (P<0.000001), which the authors attributed to the germination of naturally occurring seeds in the soil seed bank. There was no difference in soil water content between microhabitats. For upland sites, where the authors assumed there were no naturally occurring Japanese knotweed seeds, germination rates ranged from 21% to 79%. Low germination rates in some of the upland sites was attributed to dense herbaceous cover that may have inhibited seed germination or increased early seedling mortality. The authors concluded that Japanese knotweed has the potential to establish from seed in field settings and it is not limited to riparian sites [16].

Bohemian knotweed: Bohemian knotweed seeds were collected in the Pacific Northwest and germinated in a laboratory [115], though details from this study are lacking. Laboratory experiments in Massachusetts found that Bohemian knotweed seeds took 11 to 55 days to germinate [46].

All 3 knotweeds: In Pennsylvania, wild-collected seeds from a population with all 3 knotweeds were stored varying lengths of time under 3 environmental conditions: warm (64 °F (18 °C))-dry , cold (37 °F (3 °C))-dry , and cold (37 °F (3 °C))-moist. Seed wings were removed from some seeds. Germination ranged from 60% to 100%, averaging 91%. There were significant differences in germination due to seed source, seed wing removal, and environmental conditions over time (P=0.05). Cold-moist storage yielded the highest germination, averaging 95%, though germination for the other environmental conditions was still high, averaging 89% [87].

More info for the term: presence

Seeds of the 3 knotweeds may be dispersed by wind, birds, insects, or water. One review reports that the presence of a persistent, winged perianth and an abscission zone suggest wind-dispersal of Japanese knotweed seeds [11]. Giant knotweed seeds are wind-dispersed in its native range [129]. In Pennsylvania birds and insects consumed giant and Japanese knotweed seeds, which the author suggested may indicate potential dispersal mechanisms [87]. Near Washington, DC, Japanese knotweed seeds were washed downstream in floods [103]. In Belgium, the majority of Japanese knotweed seeds fell within the vicinity of the parent plant, though seedfall patterns indicated the potential for dispersal beyond 52 feet (16 m) for a small amount of seeds [126]. As of this writing (2010) no information was available regarding the dispersal of Bohemian knotweed seeds.

More info for the terms: breeding system, dioecious, gynodioecious, monoecious, perfect

Pollination: The 3 knotweeds are insect-pollinated. In Pennsylvania they were pollinated by bees, ants, butterflies, and beetles [87]. Near Washington, DC, Japanese knotweed was pollinated by bees [103].

Breeding system: Reports of the breeding systems of the 3 knotweeds are conflicting. For a review of their breeding systems, see [46]. One review that considered plants and herbarium specimens from North America reports that Japanese knotweed is gynodioecious [7]. Another review reports that Japanese knotweed is functionally dioecious in the United States, while it is gynodioecious in the United Kingdom [87]. A third review describes the Japanese knotweed breeding system as "leaky" dioecious or subdioecious in North America because populations contain both male and female plants that maintain vestigial reproductive parts of the other sex [53]. A flora from the Pacific Northwest reports Japanese knotweed as generally monoecious [58]. Giant knotweed is reported as dioecious in the United States [58] or gynodioecious in the United Kingdom [3]. In Pennsylvania, the majority of plants from a population containing all 3 knotweeds had male-fertile and female-fertile flowers on separate plants and relatively few perfect flowers were found [87].

The sexual characteristics of a particular population have important implications for the viability of seeds. In Pennsylvania, viable seeds of the 3 knotweeds were not found when male-fertile plants were absent from the site, but many viable seeds were produced when both female and male-fertile plants were present [87]. In New Jersey, one researcher found Japanese knotweed populations of both sexes and other populations of just females; female-only populations produced seeds but they were not viable [74].

More info for the terms: adventitious, eruption, litter, rhizome, root crown

The ability for multiple plant parts to regenerate vegetatively plays an important role in the spread and establishment of the 3 knotweeds. Vegetative regeneration is possible from multiple plant parts, including rhizomes, aboveground stems, roots, and leaves.

Japanese knotweed rhizomes and roots.

Rhizomes: Giant [42,121,136], Japanese [11,49,94,103,142], and Bohemian [31] knotweed are rhizomatous. As much as two-thirds of a Japanese knotweed plant's biomass exists underground in rhizomes (review by [7]). This morphology facilitates early spring emergence and rapid growth (review by [102]) and provides sufficient reserves for plants to survive multiple losses of aboveground parts within a growing season [101]. Rhizomes of the 3 knotweeds are capable of extensive spread both horizontally and vertically. In the Pacific Northwest, the rhizomes of all 3 knotweeds penetrated at least 7 feet (2 m) into the soil and spread laterally 23 to 65 feet (7-20 m) [115]. In the Czech Republic giant knotweed rhizomes reached 50 to 65 feet (15-20 m) in length [79].

Fragment size, soil depth, and light availability impact sprouting from rhizomes. In a study of Japanese knotweed rhizome regeneration from the Slovak Republic, even 1-inch (2-cm) rhizome fragments regenerated, at a rate of 47% one year and 70% another year. Regeneration rate was higher for larger fragments than smaller fragments; 3-inch (8-cm) fragments had a 90% regeneration rate one year and 70% another year [100].

Japanese knotweed rhizomes can sprout from various soil depths; 1-inch (2-cm) depth is optimal, but rhizomes may sprout from as deep as 3 feet (1 m) (review by [7]). In New Jersey field experiments, larger Japanese knotweed rhizomes and those planted at shallower depths produced more shoots than smaller rhizomes or those planted at greater depths. One inch (2 cm) was the optimal depth for planting, though fragments left on the surface or planted as deep as 20 inches (50 cm) were able to produce shoots. Rhizome fragments could produce shoots in as little as 11 days when planted 1 inch (2 cm) deep, or 47 days for fragments planted 20 inches (50 cm) deep [74]. In the United Kingdom, 4-inch (10-cm) rhizome fragments of Japanese knotweed were buried at 2-inch (5-cm), 6-inch (15-cm), and 10-inch (25-cm) depths. By 19 days after burial, rhizome fragments at all depths sprouted, though not all shoots from rhizomes buried at the greater depths had broken the soil surface. All rhizome fragments produced adventitious roots. Although regeneration was not prevented at the depths tested, this study found poorer performance (e.g., number of shoots/shoot length) with deeper burial [45]. Both giant and Japanese knotweed regenerated vegetatively through 20-inch (50-cm) (Japanese) and 40-inch (100-cm) (giant) -thick accumulations of volcanic ash and pumice following the eruption of Mt. Usu in Japan [130].

Light may enhance the survival of sprouting rhizomes. Near Washington, DC, Japanese knotweed rhizome fragments placed on streambank sites had higher survivorship than those placed under adjacent vegetation (P<0.05). In their second year of growth, rhizomes planted on streambanks exhibited significantly greater stem growth (P<0.001), basal stem diameter (P<0.001), and stem height (P<0.01) than rhizomes planted in the understory. Streambank sites had significantly higher light levels than understory sites (P<0.01), though understory sites had more organic matter (P<0.01) [104].

Rhizomes may sprout immediately following damage but sprouting may also be delayed for years. In a study of Japanese knotweed rhizome regeneration from the Slovak Republic, rhizome fragments sprouted as early as 1 week after planting for 3-inch (8-cm) long rhizomes and 4 weeks for 1-inch (2-cm) long rhizomes [100]. In riparian areas in northwestern Oregon, some sprouts of unidentified knotweeds did not emerge for 1 to 3 years following herbicide treatments that eliminated all aboveground growth. Field excavation of a plant that appeared to be dead revealed a 6-foot (2-m) long, 1-inch (3-cm) diameter living rhizome connected to the root crown 5 inches (13 cm) below the soil surface [116]. In New Jersey field experiments, season did not affect Japanese knotweed rhizome shoot production; shoots were produced in May, July, and September [74].

Other sources of The 3 knotweeds may regenerate vegetatively from plant parts other than rhizomes. A review of Japanese knotweed biology reports that the most vigorous shoots arise in groups from perennating buds on the root crown (review by [11]). One manager from the Pacific Northwest reported that small sections of Bohemian knotweed root crowns are capable of regeneration [31].

In Pennsylvania field experiments, perennating buds formed at the base of giant knotweed seedling stems within the first growing season; these buds were the primary site of vegetative regeneration in this study, not rhizomes [87]. In the United Kingdom 4-inch (10-cm) and 12-inch (30-cm) stem fragments of Japanese knotweed were buried at 2-inch (5-cm), 6-inch (15-cm), and 10-inch (25-cm) depths. After 28 days, some of the 4-inch (10-cm) and more of the 12-inch (30-cm) stem fragments produced shoots. Although regeneration was not prevented at the depths tested, this study found poorer performance (e.g., number of shoots/shoot length) with deeper burial [45]. In the United Kingdom, cut Japanese knotweed stems floating in a canal produced axillary shoots (review by [11]). In the Pacific Northwest, Bohemian knotweed stems rooted from stem nodes [31]. Japanese knotweed cut stems may produce adventitious roots in a few days, which may be followed by axillary shoot production (review by [11]). In the Czech Republic an unidentified knotweed reportedly established from fallen leaves (Brabec 1997 as cited in [15]) though this trait has not been documented elsewhere in the literature (2010).

Root sprouting has been documented for giant knotweed. In Pennsylvania, giant knotweed seeds were planted in fields under various experimental conditions, including 3 shade levels (0%, 30%, and 63%), 2 leaf litter conditions (absent, present), and 2 seed sources. The emerging seedlings were clipped to examine their ability to sprout under the various conditions. Many of the clipped giant knotweed seedlings sprouted from the roots by June of the following year. Root sprouting was not influenced by shade treatment but failed in treatments with litter. Root sprouts grew an average of 21.2 inches (53.7 cm) in the year after clipping; the tallest was 56.7 inches (144.0 cm). Root sprouts also produced flowers and a few seeds by the end of their first growing season. The authors concluded that root reserves acquired within the first growing season were sufficient for perennial growth the next year [87].

More info for the term: breeding system

• Vegetative regeneration
• Pollination and breeding system
• Seed production
• Seed dispersal
• Seed banking
• Germination
• Seedling establishment and growth
• Plant growth

It is generally accepted that asexual reproduction is the primary mode of reproduction in North America for these 3 knotweeds [74,103], though there are some reports of reproduction by seed (see Seedling establishment and growth). Near Washington, DC, 400 Japanese knotweed shoots were excavated at the periphery of stands, and all were attached to existing plants via rhizomes. No seedlings were found [103]. In Massachusetts, Japanese knotweed populations seemed to reproduce both sexually and asexually [53].

More info on this topic.

More info for the term: geophyte

Raunkiaer [95] life form:
Geophyte

Follow this link to the U.S. Forest Service Fire Effects Information Service to see a table with fire regime information that may be relevant to habitats in which this species occurs

As of 2010, there was very little information related to seed banking of the 3 knotweeds. All available information was related to seed longevity of wild-collected Japanese knotweed seeds. Japanese knotweed seeds from Massachusetts retained up to 100% viability for 4 to 16 months after indoor storage [44], while those from New Jersey rarely germinated after 1 year of storage [74]. In established stands of Japanese knotweed in Pennsylvania, the emergence of high numbers of Japanese knotweed seedlings suggested seedlings originated from the soil seed bank [16]. See Germination for more details of this study.

Though seed production of the 3 knotweeds has been documented in North America, it is not clear how representative this information is for all populations. Even if seeds are produced, they may or may not be viable. In the Pacific Northwest, the seeds of giant and Japanese knotweed were largely infertile while Bohemian knotweed seeds were viable [115]. In New Jersey, Japanese knotweed populations produced seeds but they were not viable [74]. One review reports that though giant knotweed produces seeds, seeds do not mature in temperate zones [118].

In areas with all 3 knotweeds in Pennsylvania, single stems produced 50,000 to 150,000 seeds annually; millions of seeds were produced over a 108-ft² (10-m²) area in some locations [87]. Based on field observations in Pennsylvania, 1 Japanese knotweed stem was capable of producing over 127,000 seeds/year if all flowers were pollinated and seeds set. Consequently, a single seed-bearing plant with 10 stems/plant would be capable of producing more than a million seeds/year [16]. Giant knotweed seedlings from 2 field locations in Pennsylvania produced both flowers and seeds within 3 months of emergence [87].

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More info for the terms: phenology, rhizome

In North America, giant knotweed flowers from July to October [42], with some regional variation [78,85,94,121,150]. In North and South Carolina, giant knotweed produces fruit from August to October [94]. In Pennsylvania, seeds are mature in September [87]. Giant knotweed overwinters via an underground woody rhizome (review by [7]). In the Pacific Northwest, giant knotweed growth begins in April and stems may grow 15 feet (4.5 m) by June [115].

Japanese knotweed flowers from June through August in Pennsylvania [16]; August to September in Illinois [85], the Great Plains [51], and New England [78]; and August to October in Kentucky [56]. In Pennsylvania, Japanese knotweed fruit begins to form in late August [16] and matures in September [87]. In the eastern United States, fruits generally remain on plants through the winter. Leaves are photosynthetically active until autumn frosts prompt senescence. Leaves drop throughout the winter months. Assimilation of resources shifts from shoots to roots near the end of the growing season, as the plant prepares for overwintering (review by [7]). Near Washington, DC, Japanese knotweed plants allocated most resources to aboveground growth until approximately 30 July. Through most of August, resources were allocated equally to both aboveground and belowground parts. After 28 August, most resources were allocated to belowground parts [103]. In the eastern United States, Japanese knotweed seedlings emerge in mid-spring (late March to May) depending on latitude and altitude. Rhizome sprouts emerge from late spring through mid-summer until the canopy closes (review by [7]).

As of this writing (2010) little information is available regarding the phenology of Bohemian knotweed. In the Pacific Northwest, Bohemian knotweed growth begins in April [115]. It probably flowers in the late summer and early fall like giant and Japanese knotweed, because seeds of all 3 species were mature in September in Pennsylvania [87]. Bohemian knotweed overwinters via an underground, woody rhizome (review by [7]).

Flowering Jul-Oct.

Giant, Japanese, and Bohemian knotweed are listed as noxious in several states. Information on state-level noxious weed status of plants in the United States is available at Plants Database.

Canada

Rounded National Status Rank: NNA - Not Applicable

United States

Rounded National Status Rank: NNA - Not Applicable

Rounded Global Status Rank: GNR - Not Yet Ranked

More info for the terms: allelopathy, cover, density, fire management, fitness, fresh, invasive species, litter, natural, prescribed fire, rhizome, shrub, tree

Impacts: Studies in both North America and Europe have documented a decrease in native plant cover or species richness in areas where giant [13,57,136], Japanese [13,48,57,77], or Bohemian [13,57] knotweed have established. Mechanisms suggested for native plant exclusion include the accumulation of leaf and stem litter (review by [53]), nutrient (review by [52]) and light ([107], reviews by [52,53]) limitation, and allelopathy [107,143].

Stand of Bohemian knotweed in Washington.
Photo courtesy of 10,000 Years Institute, www.10000yearsinstitute.org

Establishment of giant [136] and Japanese [72] knotweed may lead to changes in leaf litter dynamics. Japanese knotweed establishment may lead to high levels of some soil nutrients [29,30]. Studies in North America and Europe have documented changes in faunal communities, including a decrease in the diversity and abundance of invertebrates in areas with giant [66,128] and Japanese [48,72] knotweed, and a decrease in the abundance and fitness of green frogs in an area with Japanese knotweed [77]. Changes in fungal assemblages were reported in areas with Japanese knotweed [72]. In contrast, one study in Idaho found that instream leaf decomposition rates, microinvertebrate colonization, abundance, and species richness of some types of microinvertebrates did not differ in leaf litter containing Japanese knotweed compared to litter containing leaves of native gray alder and black cottonwood [14].

One study supported the assertion that giant knotweed displaces riparian species and has cascading effects on the structure and function of riparian systems. In northwestern Washington, riparian forests with higher giant knotweed stem density had lower juvenile conifer (P<0.01), juvenile red alder (P<0.001), juvenile broadleaved tree (P<0.001), and shrub (P<0.01) stem density; lower herb (P<0.01) and native herb (P<0.001) cover; and lower shrub (P=0.001), herb (P<0.001), and native herb (P=0.002) species richness compared to forests with lower giant knotweed stem density. Total mass of autumn litterfall did not differ between plots with and without established giant knotweed, but sites with giant knotweed had 70% loss in leaf litter mass of native species (P<0.001). Giant knotweed and native species differed greatly in C:N ratios in fresh and senescent leaves. Fresh giant knotweed leaves had 61% to 65% lower C:N ratios than red alder and willow leaves. In contrast, senescent giant knotweed leaves had 38% to 58% higher C:N ratios than leaves of native taxa. Estimates of nitrogen reabsorption prior to litterfall were high for giant knotweed (76%) and low for native species (red alder (5%) and willow (33%)). Consequently, areas dominated by giant knotweed had less nitrogen available for uptake by both terrestrial and aquatic organisms than areas dominated by native species. The authors suggested that changes in native species density and diversity and differences in litter quality resulting from giant knotweed establishment likely have cascading effects on the structure and function of riparian systems, though this hypothesis was not tested [136].

In old fields in south-central New York, one study examined how changes in plant diversity and stand structure resulting from Japanese knotweed establishment negatively impacted the foraging success of green frogs. Green frogs in areas with established Japanese knotweed failed to gain mass, while more than 50% of green frogs in areas without established Japanese knotweed gained mass. The authors suggested that the lower success of green frog foraging was due to declines in populations of invertebrate prey, though this hypothesis was not tested. The authors did document several changes in vegetative characteristics that could have influenced invertebrate populations and the ability of green frogs to forage. No native plants were found 33 feet (10 m) inside Japanese knotweed stands. Vegetation height increased abruptly at the edge of Japanese knotweed stands, from an average of 33 inches (84 cm) outside the stand to an average of 78 inches (198 cm) at the stand's edge. Average height to first leaves was higher in Japanese knotweed stands compared to vegetation outside of stands. Litter was deeper in Japanese knotweed stands, with most litter material consisting of large, fibrous stems [77].

Other ecological impacts of the 3 knotweeds include reduced recruitment of in-stream woody debris (review by [111]) and reduced habitat quality for wildlife (reviews by [52,87,111]). Establishment of these knotweeds may also increase the risk of streambank erosion [12] or flooding when decaying shoots are washed into rivers during high flows (reviews by [7,87]). Rhizomes and shoots may displace foundations, walls, pavement, and drainage works (review by [7]) or limit recreational access to riparian areas ([39], review by [52]). In the United Kingdom, lack of Japanese knotweed control in urban areas may lead to an increased risk of an area being "used as an illicit litter dump or as a refuge for vandals and muggers" [101].

Control: In all cases where invasive species are targeted for control, the potential for other invasive species to fill their void must be considered, no matter what control method is employed [18]. Control of biotic invasions is most effective when it employs a long-term, ecosystem-wide strategy rather than a tactical approach focused on battling individual invaders [75]. Information presented in the following sections may not be comprehensive and is not intended to be prescriptive in nature. It is intended to help managers understand the ecology and control of the 3 knotweeds in the context of fire management. For more detailed information on the control of giant, Japanese, or Bohemian knotweed, consult the references cited here or local extension services. For a review of control recommendations for the 3 knotweeds in the Pacific Northwest, including commentary on hand cutting, mowing, digging, covering, goat browsing, and many methods of herbicide application, see [115]. For a review of control methods for Japanese knotweed in the United Kingdom plus information on preventing establishment, see [24].

Several sources suggest that the 3 knotweeds are difficult to eradicate [31,59,98,109,142] due to their extensive root and rhizome systems [115], the ability of multiple plant parts to regenerate vegetatively [31,115], sprouting immediately [115,116] or 1 to 3 years after treatment [116], and the large scale of stand establishment [115]. Control of the 3 knotweeds may require multiple treatments within a single growing season [101,115,116] or several years of treatment ([103,109,115,116], review by [24]) to be effective. Careful disposal of removed plant parts is important to prevent downstream transport [31] or reestablishment. Control and eradication efforts always face the potential for floods or high water to expose and/or transport buried rhizomes or propagules from upstream populations [109].

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

Prevention: One way to minimize the establishment and spread of the 3 knotweeds is to avoid planting them. The Tennessee Exotic Pest Plant Council recommends the following native plant species as alternatives to Japanese knotweed in landscaping: goat's-beard (Aruncus dioicus), Culver's root (Veronicastrum virginicum), white snakeroot (Ageratina altissima), black cohosh (Actaea racemosa), coastal sweetpepperbush (Clethra alnifolia), and Virginia sweetspire (Itea virginica) [123]. Native alternatives to Japanese knotweed in the mid-Atlantic states include Virginia sweetspire, coastal sweetpepperbush, maleberry (Lyonia ligustrina), silky dogwood (Cornus amomum), fragrant sumac (Rhus aromatica), or flameleaf sumac (R. copallinum) [122].

It is commonly argued that the most cost-efficient and effective method of managing invasive species is to prevent their establishment and spread by maintaining "healthy" natural communities [75,106] (e.g., avoid road building in wildlands [133]) and by monitoring several times each year [64]. Managing to maintain the integrity of the native plant community and mitigate the factors enhancing ecosystem invasibility is likely to be more effective than managing solely to control the invader [59].

Weed prevention and control can be incorporated into many types of management plans, including those for logging and site preparation, grazing allotments, recreation management, research projects, road building and maintenance, and fire management [134]. See the Guide to noxious weed prevention practices [134] for specific guidelines in preventing the spread of weed seeds and propagules under different management conditions.

Cultural control: No information was available as of this writing (2010).

Physical or mechanical control: For a review of mechanical control recommendations for the 3 knotweeds in the Pacific Northwest see [115]. Physical or mechanical control of the 3 knotweeds is complicated by extensive rhizome systems that allow plants to regenerate after single or multiple mechanical control attempts [101,103,115]. In the Pacific Northwest, the 3 knotweeds sprouted following cutting, mowing, and digging, sometimes within a week of mechanical treatments [115]. In the United Kingdom, cut Japanese knotweed stems produced new shoots from dormant buds on the "rootstock". Plants cut twice over 2 years had sufficient reserves in the rhizomes for "vigorous" regeneration [101]. Also in the United Kingdom, cutting Japanese knotweed stands increased both the lateral spread of clumps and stem density (review by [11]).

Hand-pulling was considered an ineffective means of Japanese knotweed control in the United Kingdom (review by [11]). In the United Kingdom, 3 years were needed to eradicate 2 small Japanese knotweed plants by hand pulling. In established riverbank stands, 10 years of hand pulling reduced Japanese knotweed cover but did not eliminate it. Two years of biweekly mowing in the growing season were considered effective at controlling Japanese knotweed [5]. In greenhouse studies near Washington, DC, grubbing was not an effective control strategy for Japanese knotweed; it did not remove all rhizome fragments and Japanese knotweed was able to regenerate. Grubbing also exposed large amounts of mineral soil, facilitating the establishment of other nonnative plants [103]. In the Czech Republic, mowing twice in the growing season and both high- and low-intensity grazing by domestic sheep and goats were effective at reducing the survival of planted rhizomes of all 3 knotweeds (P<0.001) [15].

In greenhouse studies near Washington, DC, cutting of Japanese knotweed stems originating from rhizome fragments led to a decrease in belowground biomass when the plants were cut between 5 June and 28 August (P<0.05). Multiple cuttings led to greater decreases in belowground biomass. In this experiment, 5 cuttings were needed to cause a net depletion of belowground biomass. The authors suggested that cutting should be done at least 8 weeks prior to senescence; otherwise the treatment would have no impact on underground reserves [103].

Covering or smothering the 3 knotweeds has had variable results. Field observations in New Jersey documented one Japanese knotweed plant emerging through 3 inches (8 cm) of asphalt [74]. A horticultural journal reports that giant and Japanese knotweed may push through 2 inches (5 cm) of asphalt but suggests that smothering giant and Japanese knotweed plants with several layers of black plastic topped with asphalt, gravel, or patio stones may be an effective control method [92]. One source from the Pacific Northwest reports that covering patches of the 3 knotweeds is not an effective control method [115].

Industrial composting methods kill all plant parts of Japanese knotweed, but home compost piles are not likely to reach lethal temperatures [32].

Biological control: Biological control of invasive species has a long history that indicates many factors must be considered before using biological controls. Refer to these sources: [137,149] and the Weed control methods handbook [132] for background information and important considerations for developing and implementing biological control programs.

Managers in the United Kingdom are actively pursuing biocontrol programs for Japanese knotweed [105]. Insects from its native range may be useful in controlling Japanese knotweed ([145], review by [24]). In North America, signs of insect herbivory are low for Japanese [23] and Bohemian [107] knotweed. One source identified a number of potential insect, slug, and snail biocontrol agents for "knotweeds" in North America, though field observations in New York, Oregon, and Washington suggested that herbivore damage was low [52].

Chemical control: Herbicides are effective in gaining initial control of a new invasion or a severe infestation, but they are rarely a complete or long-term solution [21]. See the Weed control methods handbook [132] for considerations on the use of herbicides in natural areas and detailed information on specific chemicals.

Several sources suggest that herbicide application is the most effective means of controlling the 3 knotweeds in North America [31,73,109,111,112], though their establishment in riparian areas presents challenges to chemical control programs [73,111] and multiple years of treatment are needed [31,109,110]. For reviews of Japanese knotweed response to herbicides and other chemicals see the following sources: [7,11,101]. For information on intensive programs to chemically control the 3 knotweeds in North America, see the following sources: [31,40,73,109,110,111,112].

The 3 knotweeds may sprout in the growing season following some herbicide applications [31,110,115]. In Washington, numerous Bohemian knotweed root crowns sprouted the growing season following foliar herbicide application. Follow-up cut-stem treatments and stem injection treatments in the 2nd and 3rd season after initial treatment successfully killed plants, though some stems still survived into the 4th season [31].

Along the Hoh River in northwestern Washington, herbicide injection treatments reduced the number of Bohemian knotweed plants, but the resulting shift from large, multi-stemmed clumps of Bohemian knotweed to small, single-stem clumps made location of plants and subsequent control efforts difficult [112]. Effective management required large crews, intensive surveys and mapping, and multiyear efforts, all with the possibility that floods or high water might transport plants from upstream to control sites or expose buried rhizomes [109]. Managers also reported some concern that the injected herbicide could spread into adjacent soils and harm nearby native vegetation. Managers concluded that Bohemian knotweed eradication would likely take ≥10 years in this area [111].

Integrated management: Several sources report the use of integrated management techniques in the control of the 3 knotweeds. Along roadsides in New York, one author recommended management strategies that included both direct control of Japanese knotweed and the promotion of native vegetation [73]. In riparian areas in northwestern Oregon, managers used patch size, patch location, time of year, and landowner preference to determine control strategies for Japanese and giant knotweed. Integrated methods included foliar and stem herbicide application, spring stem cutting, and manual removal and digging of rhizomes. Adaptive management led to a 89.6% reduction in number of stems over 8 years of treatments. However, control efforts were not successful in eradicating any patch with >573 stems through the use of any treatment regime, even after up to 9 treatments [116]. Reports from Europe suggest that using a combination of mechanical digging and herbicide application led to a greater reduction in Japanese knotweed plant density, plant height, stem diameter, and number of leaves than either treatment alone [25].

These species are introduced in Switzerland.