Submitted Successfully!
To reward your contribution, here is a gift for you: A free trial for our video production service.
Thank you for your contribution! You can also upload a video entry or images related to this topic.
Version Summary Created by Modification Content Size Created at Operation
1 + 2688 word(s) 2688 2021-12-28 03:26:13 |
2 format correct Meta information modification 2688 2021-12-31 02:16:07 |

Video Upload Options

Do you have a full video?

Confirm

Are you sure to Delete?
Cite
If you have any further questions, please contact Encyclopedia Editorial Office.
Kato-Noguchi, H. Allelopathy of Knotweeds as Invasive Plants. Encyclopedia. Available online: https://encyclopedia.pub/entry/17642 (accessed on 16 April 2024).
Kato-Noguchi H. Allelopathy of Knotweeds as Invasive Plants. Encyclopedia. Available at: https://encyclopedia.pub/entry/17642. Accessed April 16, 2024.
Kato-Noguchi, Hisashi. "Allelopathy of Knotweeds as Invasive Plants" Encyclopedia, https://encyclopedia.pub/entry/17642 (accessed April 16, 2024).
Kato-Noguchi, H. (2021, December 30). Allelopathy of Knotweeds as Invasive Plants. In Encyclopedia. https://encyclopedia.pub/entry/17642
Kato-Noguchi, Hisashi. "Allelopathy of Knotweeds as Invasive Plants." Encyclopedia. Web. 30 December, 2021.
Allelopathy of Knotweeds as Invasive Plants
Edit

Perennial herbaceous Fallopia is native to East Asia, and was introduced to Europe and North America in the 19th century as an ornamental plant. Fallopia has been spreading quickly and has naturalized in many countries. It is listed in the world’s 100 worst alien species. Fallopia often forms dense monospecies stands through the interruption of the regeneration process of indigenous plant species. Allelopathy of Japanese knotweed (Fallopia japonica), giant knotweed (Fallopia sachalinensis), and Bohemian knotweed (Fallopia x bohemica) has been reported to play an essential role in its invasion. The exudate from their roots and/or rhizomes, and their plant residues inhibited the germination and growth of some other plant species. These knotweeds, which are non-mycorrhizal plants, also suppressed the abundance and species richness of arbuscular mycorrhizal fungi (AMF) in the rhizosphere soil. Such suppression was critical for most territorial plants to form the mutualism with AMF, which enhances the nutrient and water uptake, and the tolerance against pathogens and stress conditions.

allelochemical decomposition exudation invasive plant mycorrhizal colonization monospecies stand phytotoxicity

1. Introduction

The genus Fallopia (Polygonaceae) contains highly competitive invasive species such as, Japanese knotweed (Fallopia japonica (Houtt.) Ronse Decraene; synonym: Polygonum cuspidatum Sieb. et Zucc.), giant knotweed (Fallopia sachalinensis (F. Schmidt) Ronse Decraene; synonym: Polygonum sachalinensis F. Schmidt ex Maxim), Bohemian knotweed (Fallopia x bohemica (Chrteket Chrtková) J.P. Bailey; synonym Polygonum x bohemicum (Chrtek et Chrtková) P.F. Zika et A.L. Jacobson). Japanese knotweed and giant knotweed hybridize naturally by sexual reproduction and create the hybrid Bohemian knotweed [1].
These knotweeds are fast-growing perennial herbaceous plants and form monospecific stands with dense canopy, and expand the stands through their extensive rhizome systems [2]. Japanese knotweed grows 2–3 m in height, and has multiple branches with hollow stems. Its shoots were recorded to grow 4–15 cm per day [3]. Its ovate leaves are 3–10 cm in length with a truncate base. Giant knotweed is 3–6 m in height, and has few branches with hollow stems. Its ovate leaves are 20–40 cm in length with a deeply cordate base. Characteristic of Bohemian knotweed has variations between both species [2].
Japanese knotweed grows under a wide range of soil pH, and nutrient poor soil conditions such as volcanic slopes as a pioneer species, and in disturbed areas such as roadsides and pastures [4][5][6]. Giant knotweed occurs in riparian corridors, coastal cliffs, road banks, and bare soils in human settlements [3]. Those knotweeds show a strong preference for man-made disturbed habitats, and along roads, and watercourses are their most frequent habitats. However, Bohemian knotweed has the highest population in man-made habitats [7][8].
Knotweeds spread sexually and asexually. The seeds of knotweeds are buoyant, and carried with water flow in streams and rivers for a long distance. The seeds are also easy to disperse with the wind [9][10]. The seed distribution may contribute to establishing knotweed populations in new habitats. Knotweeds also propagate with their rhizome branches. The rhizomes grow quickly, and the apex of the rhizome branches develops into an aerial shoot and forms a new shoot clump [4]. Rhizome fragments made by such as floods and human activities, as small as 1 cm in length and 0.7 g fresh in weight can regenerate new plants [11]. The fragmentation and subsequent regeneration increase their propagation potential.
The native range of Japanese knotweed is China, Japan, Korea, and Taiwan, and giant knotweed is native to Sakhalin Island, North Japan, and Korea [2]. Both species were introduced into Europe in the 19th century as ornamental plants and collections for botanical gardens, and were sold to gardens and parks in various countries [2][12]. Japanese knotweed was also cultivated as a Chinese medicinal plant [13]. Giant knotweed was recommended as riverbank stabilizer and livestock feed [14]. Although hybrid species, Bohemian knotweed was first recorded in Europe around 1980s, it was considered to occur in the late 19th century and spread undetectably [15]. The Japanese knotweed and giant knotweed were not sympatric in the native range. However, Bohemian knotweed was also observed in Japan in 1997 [16]. Japanese knotweed is the most widespread species in Europe, and followed by Bohemian knotweed and giant knotweed [8][17].
Japanese knotweed and giant knotweed were introduced into North America in the 19th century. The presence of Bohemian knotweed was first recognized in 2001 from Seattle, USA [18]. The presence of the knotweeds has been confirmed in 42 states including Alaska and 8 provinces in Canada [19][20]. These knotweeds were also confirmed in Australia, New Zealand, South Africa, and other countries [15][16]. Knotweed species have already naturalized in many countries as invasive noxious weeds, and are listed in the world’s 100 worst invasive alien species [21].
The characteristics of life-history of plants, such as high growth and high reproduction rate, and phenotypic plasticity are involved in the naturalization of invasive plants into the introduced range [22][23][24]. As described above, knotweeds grow fast and reproduce sexually and asexually. Those species can grow under poor soil conditions and in disturbed places. The single stem of Japanese knotweed bore about 200,000 seeds, and the germination rate was 50–80% [25][26]. Soil collected from the invaded site of Bohemian knotweed contained about 800 seeds/m2 [27]. Genetic diversity of each knotweed species is not clear. However, knotweeds showed large epigenetic differentiation and phenotypic plasticity in response to several environmental conditions [28][29]. Epigenetics diversity provides clonal plants with the potential for acclimation in various environmental conditions [30]. Hybridization of Japanese knotweed and giant knotweed probably gives genetic diversity to a hybrid plant, Bohemian knotweed [1][31][32].
High defense capacity against pathogens and herbivores contributes for the invasive plants to naturalize into introduced range [33][34][35]. Japanese knotweed has a lower abundance and diversity of invertebrate herbivores compared to native plant species of introduced range, and received less leaf damage than their native plant species [36]. Knotweed contains flavones, quinones, and stilbenes [13][37], and some of these compounds may act as defensive agents against herbivores and pathogens. In addition, aqueous extracts of rhizomes of Japanese knotweed altered soil fauna and reduced nematode population [38].

2. Allelopathy of Knotweeds

Allelopathy is the interaction between one plant and other neighboring plants through the specific secondary metabolites which are defined as allelochemicals [39]. The allelochemicals are released into their rhizosphere soil and neighboring environments either by root exudation, decomposition of plant residues, rainfall leachates, or volatilization from living plant parts [40][41][42].
Plant-to-plant interaction is a complex combination of competition for resources such as water, nutrients, and light, along with allelopathic interaction through allelochemicals [43][44]. Thus, it is essential to eliminate such competitive effects from experimental systems to clarify allelopathy [45][46][47]. Bohemian knotweed reduced the growth and survival rate of native plant species, Eupatorium perfoliatum L. and Acer saccharinum L. in field conditions. Supplemental nutrient and light to the growth conditions for those native plants recovered the inhibitory effects of the knotweed, but the recovery was limited. Therefore, allelopathy of Bohemian knotweed may contribute to a certain extent of the reduction in the growth and survival rate of the native plant species [48].
A rhizome (contain single node) of Bohemian knotweed and each of six native plant species (four forbs; Geraniun robertianum L., Lamium maculatum L., Silene dioica (L.) Clairv. and Symphytum officinalis L.; and two grasses; Lolium perenne L. and Poa trivialis L.) were grown together in 7 L pots filled with soil for three weeks. The rhizome of Bohemian knotweed significantly suppressed the growth of four forbs but not grasses. Activated carbons mixed with soil in the pots reduced the inhibitory effects of the knotweed on the forbs [37]. Activated carbon absorbs organic compounds in the soil [49]. Therefore, the result indicates that allelochemicals released from the rhizome of Bohemian knotweed may be involved in the inhibition. The evidence of allelopathy of knotweeds has been accumulated over three decades. In this section, allelopathic potential of the exudation, extracts, and plant residues of knotweeds was summarized (Table 1).
Table 1. Allelopathic activities of roots, rhizomes, and above-ground parts of knotweeds.
Source   Knotweed Target Plant Species Inhibition Reference
Root, rhizome          
  Exudation Japanese knotweed Salix viminalis, Salix atrocinerea, Populus nigra Growth [50]
    Giant knotweed Lactuca sativa Growth [51]
  Rhizome extract Japanese knotweed
Giant knotweed
Bohemian knotweed
Leucosinapis alba Growth [52]
    Japanese knotweed
Bohemian knotweed
Raphanus sativus Growth
Germination
[53][54]
    Japanese knotweed Atrichum angustatum
Thuidium delicatulum
Biomass [55]
Above-ground part          
  Leaf residue Japanese knotweed
Giant knotweed
Bohemian knotweed
Leucosinapis alba
Brassica napa
Germination [56]
  Leaf extract Japanese knotweed
Giant knotweed
Bohemian knotweed
Urtica dioica
Calamagrostis epigejos
Lepidium sativum
Germination [57]
  Soaking water Japanese knotweed Triticum aestivum
Sinapis arvensis
Germination [58]
  Extract (whole part) Japanese knotweed
Giant knotweed
Brassica napa, Avena sativa
Helianthus annuus
Growth [59]

2.1. Exudation

Japanese knotweed was grown in “donor pots”, and test plants (Salix viminalis L., Salix atrocinerea Brot. and Populus nigra L.) were grown in “target pots”. Test plants were irrigated with drain solution from the donor pots and with additional nutrient-enriched solution, and incubated for four months. The system could discriminate resource competition between Japanese knotweed and test plants. The growth of those test plants was suppressed by the drain solution from Japanese knotweed. The drain solution contained polyphenol compounds, but those compounds were not identified [50]. Giant knotweed (donor plant) and Lactuca sativa L. seedlings (receiver plant) were incubated with root exudate recirculating system [60] for 10–14 days. Exudate from roots and rhizomes of giant knotweed significantly inhibited the growth of L. sativa seedlings [51]. According to those observations, exudation from rhizome and/or roots of those knotweeds may contain allelochemicals, which cause the suppression of the growth of the test plant species. Although the organs that synthesize those allelochemicals are unknown, certain allelochemicals may be released from rhizomes and/or roots of knotweeds. Therefore, the evaluation of allelopathic potential of extracts of rhizome and/or roots is necessary.
Aqueous rhizome extracts of Japanese knotweed, giant knotweed, and Bohemian knotweed inhibited the root and hypocotyl growth of Leucosinapis alba (L.) Spach. However, the inhibitory effects of three extracts were not significantly different [52]. Aqueous rhizome extracts of Japanese knotweed and Bohemian knotweed also delayed the germination of Raphanus sativus L., and suppressed their growth. The roots of R. sativus showed symptoms of oxidative stress such as abnormal shapes of nuclei, plasma membrane, mitochondria, and endoplasmic reticulum [53][54]. Aqueous rhizome extracts of Japanese knotweed (Polygonum cuspidatum s.l.) inhibited the biomass of the mosses, Atrichum angustatum (Brid.) Bruch and Schimp. and Thuidium delicatulum (Hedw.) Schimp. [55]. Those findings indicate that the rhizomes of knotweeds may contain allelochemicals, and those allelochemicals are extractable.

2.2. Plant Residues

Japanese, giant, and bohemian knotweeds are perennial herbaceous plants, but above-ground parts of the knotweeds die back at the first frost in the winter season [21]. Those above-ground parts decay and accumulate as a litter layer on the soil. During the decomposition process of the litter, some of the secondary metabolites may be liberated into rhizosphere soil and act as allelochemicals [40][41][42]. Therefore, evaluation of the allelopathic potential of above-ground parts of knotweeds is also necessary.
Leaves of Japanese knotweed, giant knotweed, and Bohemian knotweed were shattered into small pieces and mixed with soil, and the seeds of Leucosinapis alba (L.) Spach, Brassica napa L., Chenopodium album L., and Echinochloa crus-galli (L.) P.Beauv were sown into the mixture. The germination of L. alba and B. napa was significantly suppressed by the residues of those knotweed leaf residues. The inhibitory activity of the residue of Japanese knotweed was the highest. However, all residues did not significantly inhibit the germination of C. album and E. crus-galli [56]. Aqueous leaf extracts of Japanese knotweed, giant knotweed, and Bohemian knotweed inhibited the germination of Urtica dioica L., Calamagrostis epigejos (L.) Roth, and Lepidium sativum L. However, the inhibitory effect of Japanese knotweed was the least [57]. Senescent above-ground parts of Japanese knotweed were soaked in water. Seeds of Triticum aestivum L. and Sinapis arvensis L. were sown into the soil, and irrigated with the soaking water of the Japanese knotweed every two days for two weeks. The irrigation of the soaking water resulted in significantly reduction in their germination [58]. Aqueous extracts of whole plants of Japanese knotweed and giant knotweed also inhibited the growth of Brassica napa L., Avena sativa L., and Helianthus annuus L. [59]. Those findings indicate that above-ground parts of those knotweeds may contain allelochemicals. Those compounds may be released into the soil during the decomposition process of the plant residues. However, the efficiency of allelopathic potential among Japanese knotweed, giant knotweed, and Bohemian knotweed is not able to compared because of the limited information.

3. Invasion and Allelopathy of Knotweeds

Perennial plants are able to release allelochemicals into the rhizosphere soil over several years through the decomposition process of plant parts including fallen leaves, and the exudation from their rhizomes and roots, and those allelochemicals may be able to accumulate in the soil [61][62][63][64][65][66][67]. The invasion of perennial herbaceous species, knotweed significantly reduced the plant diversity and abundance of native herbs, shrubs, and juvenile trees in the introduced range [68][69]. The invasion of knotweed also suppressed long-term native tree regeneration and shifted from tree-dominated riparian forests to knotweed-dominated herbaceous shrublands [70].
According to the novel weapon hypothesis, some invasive plant species may have particularly strong allelopathic activity and success in their invasion into the introduced range. Allelopathy of the invasive plants is mediated by allelochemicals that are new to the plant species in the introduced range. Those indigenous plants species in the introduced range are susceptible to the allelochemicals. The plants that co-evolved with invasive plants had the opportunity to obtain the defense systems against those allelochemicals. However, the plant species in the introduced range have not obtained the defense systems that obviate those allelochemicals [71][72]. Root powder of Japanese knotweed suppressed the germination of Ulmus minor Mill. (native in Europe), but did not suppress the germination of Ulmus parvifolia Jacq. (native in East Asia, same as knotweed) [73]. The concentrations of piceid (10) and resveratrolside (11) in Japanese knotweed from Switzerland (introduced range) were higher than in those from China (native range) [74]. Those observations may support the novel weapon hypothesis for the invasive plant species.
In addition, the invasion of Japanese knotweed reduced the abundance and species richness of arbuscular mycorrhizal fungi (AMF) [75]. Root powder of Japanese knotweed also inhibited AMF vesicle formation in Ulmus spp. [73]. Mycorrhizal colonization is crucial for most territorial plants. AMF fungi are widespread and important mycorrhiza for plant symbionts. AMF fungi increase the ability of plants to absorb nutrient and water, and enhance the protection potential against pathogen attacks and several stress conditions [76]. Knotweeds are non-mycorrhizal plants and do not form arbuscular mycorrhiza [77][78]. Knotweeds may be able to degrade the fungal mutualism of nearby plants without negatively impacting their own nutrient and water acquisition. The reduction in AMF populations in the soil of the knotweed introduced range weakens the ability of residential plants for the competition and regeneration, and leads knotweed to dominant communities in the introduced range. Allelochemicals have the potential to inhibit plant mutualism with AMF fungi [79]. Therefore, allelochemicals released from the knotweeds may cause the reduction in AMF communities in the soil, and contribute to the knotweed invasion. The suppression by allelochemicals on AMF communities were also found in non-mycorrhizal species, Alliaria petiolate (M. Bieb.) Cavara and Grande (Brassicaceae) [80][81].
Soaking water of giant knotweed (aboveground parts) suppressed the population of soil fungal pathogens [58]. Bohemian knotweed and indigenous plant species were grown in the soil collected from knotweed-uninvaded areas. The community of soil bacteria shifted the balance in favor of the knotweed, and promoted the growth and regeneration of the knotweed more than those of indigenous plant species. This promotion effect was reduced by adding activated carbons to the soil [31]. The observation suggests that certain compounds released from the knotweed may change the balance of soil bacteria in favor of the knotweed. However, further investigation is necessary to identify those allelochemicals.
Many of the phytotoxic substances from the invasive plants have been reported to have multiple functions such as allelopathic, anti-pathogen, anti-herbivore activity, and provide the invasive plants with the advantage in the increasing their population in the introduced range [24][82][83]. Large numbers of secondary metabolites have been isolated from knotweeds, such as stilbenes, quinones, flavonoids, coumarins, and lignans [13]. Among them, for instance, emodin was reported to work as a defense compound for pathogens, herbivores, and abiotic stress factors [84]. Resveratrol and piceid may also be involved in the interaction of plant–pathogen and plant–herbivore [85][86]. Japanese knotweed plant itself was also reported to possess antipathogen and antifungal effects [13][87]. Some of those compounds may enhance competitive ability of knotweeds and make the plant invasive. As describe previously, knotweeds may interrupt the regeneration process of indigenous plant species by decreasing their germination and growth directory, and indirectly via the suppression of mycorrhizal colonization to indigenous plant species (Figure 1). In addition, the elevated temperature from 2000 to 2008 results in an increase to 35–53% of the habitat being suitable for knotweed in southern Ontario, Canada [88], indicating that global warming may increase the threat of the invasion of the species into the additional introduced areas.
Figure 1. A possible scheme of knotweed to establish the new habitats.

References

  1. Bailey, J.P.; Bímová, K.; Mandák, B. The potential role of polyploidy and hybridisation in the further evolution of the highly invasive Fallopia taxa in Europe. Ecol. Res. 2007, 22, 920–928.
  2. Bailey, J.P.; Bímová, K.; Mandák, B. Asexual spread versus sexual reproduction and evolution in Japanese knotweed s.l. sets the stage for the “Battle of the Clones”. Biol. Invasions 2009, 11, 1189–1203.
  3. Sukopp, H.; Starfinger, U. Reynoutria Sachalinensis in Europe and in the Far East: A Comparison of the Species Ecology in its Native and Adventive Distribution Range. In Plant Invasions—General Aspects and Special Problems; Pyšek, P., Prach, K., Rejmánek, M., Wade, M., Eds.; SPB Academic: Amsterdam, The Netherlands, 1995; pp. 151–159.
  4. Adachi, N.; Terashima, I.; Takahaski, M. Central die-back of monoclonal stands of Reynoutria japonica in an early stage of primary succession on Mount Fuji. Ann. Bot. 1996, 77, 477–486.
  5. Tiébré, M.S.; Vanderhoeven, S.; Saad, L.; Mahy, G. Hybridization and sexual reproduction in the invasive alien Fallopia (Polygonaceae) complex in Belgium. Ann. Bot. 2007, 99, 193–203.
  6. Rahmonov, O.; Czylok, A.; Orczewska, A.; Majgier, L.; Parusel, T. Chemical composition of the leaves of Reynoutria japonica Houtt. and soil features in polluted areas. Cent. Eur. J. Biol. 2014, 9, 320–330.
  7. Mandák, B.; Pyšek, P.; Lysák, M.; Suda, J.; Krahulcová, A.; Bímová, K. Variation in DNA-ploidy levels of Reynoutria taxa in the Czech Republic. Ann. Bot. 2003, 92, 265–272.
  8. Mandák, B.; Pyšek, P.; Bímová, K. History of the invasion and distribution of Reynoutria taxa in the Czech Republic: A hybrid spreading faster than its parents. Preslia 2004, 76, 15–64.
  9. Tiébré, M.S.; Saad, L.; Mahy, G. Landscape dynamics and habitat selection by the alien invasive Fallopia (Polygonaceae) in Belgium. Biodivers. Conserv. 2008, 17, 2357–2370.
  10. Lamberti-Raverot, B.; Piola, F.; Thiébaut, M.; Guillard, L.; Vallier, F.; Puijalon, S. Water dispersal of the invasive complex Fallopia: The role of achene morphology. Flora 2017, 234, 150–157.
  11. Brock, J.H.; Child, L.E.; Waal, L.C.; Wade, M. The Invasive Nature of Fallopia Japonica is Enhanced by Vegetative Regeneration from Stem Tissues. In Plant Invasions—General Aspects and Special Problems; Pyšek, P., Prach, K., Rejmánek, M., Wade, M., Eds.; SPB Academic: Amsterdam, The Netherlands, 1995; pp. 131–139.
  12. Drazan, D.; Smith, A.G.; Anderson, N.O.; Becker, R.; Clark, M. History of knotweed (Fallopia spp.) invasiveness. Weed Sci. 2021, 69, 617–623.
  13. Peng, W.; Qin, R.; Li, X.; Zhou, H. Botany, phytochemistry, pharmacology, and potential application of Polygonum cuspidatum Sieb.et Zucc.: A review. J. Ethnopharmacol. 2013, 148, 729–745.
  14. Bailey, J.P.; Conolly, A.P. Prize-winners to pariahs—A history of Japanese knotweed s.l. (Polygonaceae) in the British Isles. Watsonia 2000, 23, 93–110.
  15. Bailey, J.; Wisskirchen, R. The distribution and origins of Fallopia × bohemica (Polygonaceae) in Europe. Nord. J. Bot. 2006, 24, 173–199.
  16. Bailey, J.P. Japanese Knotweed s.l. at Home and Abroad. In Plant Invasions: Ecological Threats and Management Solutions; Child, L., Brock, J., Brundu, G., Prach, K., Pyšek, P., Wade, P., Williamson, M., Eds.; Backhuys Publishers: Leiden, The Netherlands, 2003; pp. 183–196.
  17. Sołtysiak, J.; Brej, T. Characteristics that make the Fallopia genus (Polygonaceae) highly invasive. Ecol. Quest. 2012, 16, 23–27.
  18. Barney, J.N. North American history of two invasive plant species: Phytogeographic distribution, dispersal vectors, and multiple introductions. Biol. Invasions 2006, 8, 703–717.
  19. USDA PLANTS Database Profile: URl: Polygonum Cuspidatum, Polygonum Sachalinense. Available online: https://plants.sc.egov.usda.gov/home/plantProfile?symbol=POCU6 (accessed on 27 October 2021).
  20. New York Invasive Species Information, Profile: Japanese Knotweed. Available online: http://nyis.info/invasive_species/japanese-knotweed/ (accessed on 27 October 2021).
  21. Global Invasive Species Database, Species Profile: Polygonum Cuspidatum. Available online: http://www.iucngisd.org/gisd/speciesname/Polygonum+cuspidatum (accessed on 27 October 2021).
  22. Thompson, J.D.; McNeilly, T.; Gray, A.J. Population variation in Spartina anglica C.E. Hubbard. I. Evidence from a common garden experiment. New Phytol. 1991, 117, 115–128.
  23. Mack, R.M. Predicting the identity and fate of plant invaders: Emergent and emerging approaches. Biol. Conserv. 1996, 78, 107–121.
  24. Cappuccino, N.; Arnason, J.T. Novel chemistry of invasive exotic plants. Biol. Lett. 2006, 2, 189–193.
  25. Bailey, J.P. The Reproductive Biology and Fertility of Fallopia Japonica (Japanese Knotweed) and its Hybrids in the British Isles. In Ecology and Management of Invasive Riparian Plants; de Waal, C., Child, L.E., Wade, M., Brock, J.H., Eds.; Wiley: Chichester, UK, 1994; pp. 141–158.
  26. Engler, J.; Abt, K.; Buhk, C. Seed characteristics and germination limitations in the highly invasive Fallopia japonica s.l. (Polygonaceae). Ecol. Res. 2011, 26, 555–562.
  27. Toews, H.P. Introduction of Native Tree Species in Sites Invaded by Japanese Knotweed Taxa and a Study of Its Affect of the Seedbank; New York State University: New York, NY, USA, 2012; pp. 1–41.
  28. Bossdorf, O.; Richards, C.L.; Pigliucci, M. Epigenetics for ecologists. Ecol. Lett. 2008, 11, 106–115.
  29. Schrey, A.W.; Alvarez, M.; Foust, C.M.; Kilvitis, H.J.; Lee, J.D.; Liebl, A.L.; Robertson, M. Ecological epigenetics: Beyond MS-AFLP. Integr. Comp. Biol. 2003, 53, 340–350.
  30. Douhovnikoff, V.; Dodd, R.S. Epigenetics: A potential mechanism for clonal plant success. Plant Ecol. 2015, 216, 227–233.
  31. Parepa, M.; Schaffner, U.; Bossdorf, O. Help from under ground: Soil biota facilitate knotweed invasion. Ecosphere 2013, 4, 31.
  32. Gaskin, J.F.; Schwarzländer, M.; Grevstad, F.S.; Haverhals, M.A.; Bourchier, R.S.; Miller, T.W. Extreme differences in population structure and genetic diversity for three invasive congeners: Knotweeds in western North America. Biol. Invasions 2014, 16, 2127–2136.
  33. Keane, R.M.; Crawley, M.J. Exotic plant invasions and the enemy release hypothesis. Trend. Ecol. Evol. 2002, 17, 164–170.
  34. Mitchell, C.E.; Power, A.G. Release of invasive plants from fungal and viral pathogens. Nature 2003, 421, 625–627.
  35. Cappuccino, N.; Carpenter, D. Invasive exotic plants suffer less herbivory than non-invasive plants. Biol. Lett. 2005, 1, 435–438.
  36. Williams, V.R.J.; Sahli, H.F. A comparison of herbivore damage on three invasive plants and their native congeners: Implications for the enemy release hypothesis. Castanea 2016, 81, 128–137.
  37. Murrell, C.; Gerber, E.; Krebs, C.; Parepa, M.; Schaffner, U.; Bossdorf, O. Invasive knotweed affects native plants through allelopathy. Am. J. Bot. 2011, 98, 38–43.
  38. Abgrall, C.; Forey, E.; Mignot, L.; Chauvat, M. Invasion by Fallopia japonica alters soil food webs through secondary metabolites. Soil Biol. Biochem. 2018, 127, 100–109.
  39. Rice, E.L. Allelopathy, 2nd ed.; Academic Press: Orlando, USA, 1984; pp. 1–422.
  40. Bais, H.P.; Weir, T.L.; Perry, L.G.; Gilroy, S.; Vivanco, J.M. The role of root exudates in rhizosphere interactions with plants and other organisms. Annu. Rev. Plant Biol. 2006, 57, 233–266.
  41. Bonanomi, G.; Sicurezza, M.G.; Caporaso, S.; Esposito, A.; Mazzoleni, S. Phytotoxicity dynamics of decaying plant materials. New Phytol. 2006, 169, 571–578.
  42. Belz, R.G. Allelopathy in crop/weed interactions—An update. Pest Manag. Sci. 2007, 63, 308–326.
  43. Qasem, J.R.; Hill, T.A. On difficulties with allelopathy methodology. Weed Res. 1989, 29, 345–347.
  44. Einhellig, F.A. Interactions involving allelopathy in cropping systems. Agron. J. 1996, 88, 886–893.
  45. Fuerst, E.P.; Putnam, A.R. Separating the competitive and allelopathic components of interference: Theoretical principles. J. Chem. Ecol. 1983, 9, 937–944.
  46. Leather, G.R.; Einhelling, F.A. Bioassay of naturally occurring allelochemicals for phytotoxicity. J. Chem. Ecol. 1988, 14, 1821–1828.
  47. Inderjit; Olosfsdotter, M. Using and Improving Laboratory Bioassays in Rice Allelopathy Research. In Allelopathy in Rice; Olofsdotter, M., Ed.; International Rice Research Institute: Manila, Philippines, 1998; pp. 45–55.
  48. Siemens, T.J.; Blossey, B. An evaluation of mechanisms preventing growth and survival of two native species in invasive Bohemian knotweed (Fallopia × bohemica, Polygonaceae). Am. J. Bot. 2007, 94, 776–783.
  49. Inderjit; Callaway, R.M. Experimental designs for the study of allelopathy. Plant Soil 2003, 256, 1–11.
  50. Dommanget, F.; Evette, A.; Spiegelberger, T.; Gallet, C.; Pacé, M.; Imbert, M.; Navas, M.L. Differential allelopathic effects of Japanese knotweed on willow and cottonwood cuttings used in riverbank restoration techniques. J. Environ. Manag. 2014, 132, 71–78.
  51. Inoue, M.; Nishimura, H.; Li, H.H.; Mizutani, J. Allelochemicals from Polygonum sachalinense Fr. Schm. (Polygonaceae). J. Chem. Ecol. 1992, 18, 1833–1840.
  52. Vrchotová, N.; Šerá, B. Allelopathic properties of knotweed rhizome extracts. Plant Soil Env. 2008, 54, 301–303.
  53. Šoln, K.; Žnidaršič, N.; Koce, J.D. Root Growth Inhibition and Ultrastructural Changes in Radish Root Tips After Treatment with Aqueous Extracts of Fallopia Japonica and F. × Bohemica Rhizomes. Protoplasma 2021.
  54. Šoln, K.; Likar, M.; Koce, J.D. Effects of rhizome extracts from invasive knotweed species Fallopia japonica and F. × bohemica on radish seed germination and root growth of seedlings. Allelopath. J. 2021, 52, 103–118.
  55. Palmeri, J.; Kiviat, E. Toxic Effects of Knotweed Polygonum cuspidatum s.l. Rhizome on the Mosses Atrichum angustatum and Thuidium Delicatulum. Lindbergia 2021, 1.
  56. Šerá, B. Effects of soil substrate contaminated by knotweed leaves on seed development. Pol. J. Env. Stud. 2012, 3, 713–717.
  57. Moravcová, L.; Pyšek, P.; Jarošík, V.; Zákravský, P. Potential phytotoxic and shading effects of invasive Fallopia (Polygonaceae) taxa on the germination of dominant native species. NeoBiota 2011, 9, 31–47.
  58. Heděnec, P.; Novotný, D.; Ust’ak, S.; Honzík, R.; Kovářová, M.; Šimáčková, H.; Frouz, J. Allelopathic effect of new introduced biofuel crops on the soil biota: A comparative study. Eur. J. Soil Biol. 2014, 63, 14–20.
  59. Novak, N.; Novak, M.; Barić, K.; Šćepanović, M.; Ivić, D. Allelopathic potential of segetal and ruderal invasive alien plants. J. Cent. Eur. Agric. 2018, 19, 408–422.
  60. Stevens, G.A.; Tang, C.S. Inhibition of seedling growth of crop species by recirculating root exudates of Bidens pilosa L. J. Chem. Ecol. 1985, 11, 1411–1425.
  61. Mallik, A.U. Allelopathy and competition in coniferous forests. Environ. Sci. 1998, 54, 309–315.
  62. Kato-Noguchi, H.; Takeshita, S.; Kimura, F.; Ohno, O.; Suenaga, K. A novel allelopathic active substance in Ginkgo biloba. J. Plant Physiol. 2013, 170, 1595–1599.
  63. Kato-Noguchi, H.; Takeshita, S. Contribution of a phytotoxic compound to the allelopathy of Ginkgo Biloba. Plant Signal. Behav. 2013, 8, e26999.
  64. Kato-Noguchi, H.; Kimura, F.; Ohno, O.; Suenaga, K. Involvement of allelopathy in inhibition of understory growth in red pine forests. J. Plant Physiol. 2017, 218, 66–73.
  65. Kato-Noguchi, H.; Kurniadie, D. Allelopathy and allelopathic substances of mango (Mangifera indica L.). Weed Biol. Manag. 2020, 20, 131–138.
  66. Kato-Noguchi, H. Phytotoxic substances involved in teak allelopathy and agroforestry. Appl. Sci. 2021, 11, 3314.
  67. Kato-Noguchi, H.; Kurniadie, D. Allelopathy of Lantana camara as an Invasive plant. Plants 2021, 10, 1028.
  68. Gerber, E.; Krebs, C.; Murrell, C.; Moretti, M.; Rocklin, R.; Schaffner, U. Exotic invasive knotweeds (Fallopia spp.) negatively affect native plant and invertebrate assemblages in European riparian habitats. Biol. Conserv. 2008, 141, 646–654.
  69. Urgenson, L.S.; Reichard, S.H.; Halpern, C.B. Community and ecosystem consequences of giant knotweed (Polygonum sachalinense) invasion into riparian forests of western Washington, USA. Biol. Conserv. 2009, 142, 1536–1541.
  70. Wilson, M.; Freundlich, A.; Martine, C. Understory dominance and the new climax: Impacts of Japanese knotweed (Fallopia japonica) invasion on native plant diversity and recruitment in a riparian woodland. Biodiv. Data J. 2007, 5, e20577.
  71. Callaway, R.M.; Ridenour, W.M. Novel weapons: Invasive success and the evolution of increased competitive ability. Front. Ecol. Environ. 2004, 2, 436–443.
  72. Bais, H.P.; Vepachedu, R.; Gilroy, S.; Callaway, R.M.; Vivanco, J.M. Allelopathy and exotic plant invasion: From molecules and genes to species interaction. Science 2003, 301, 1377–1380.
  73. Pinzone, P.; Potts, D.; Pettibone, G.; Warren, R. Do novel weapons that degrade mycorrhizal mutualisms promote species invasion? Plant Ecol. 2018, 219, 539–548.
  74. Fan, P.; Hay, A.E.; Marston, A.; Lou, H.; Hostettmann, K. Chemical variability of the invasive neophytes Polygonum cuspidatum Sieb. and Zucc. and Polygonum sachalinensis F. Schmidt ex Maxim. Biochem. Syst. Ecol. 2009, 37, 24–34.
  75. Zubek, S.; Kapusta, P.; Stanek, M.; Woch, M.W.; Błaszkowski, J.; Stefanowicz, A.M. Reynoutria japonica invasion negatively affects arbuscular mycorrhizal fungi communities regardless of the season and soil conditions. Appl. Soil Ecol. 2022, 169, 104152.
  76. Smith, S.E.; Read, D.J. Mycorrhizal Symbiosis, 3rd ed.; Academic Press: London, UK, 2008; pp. 1–815.
  77. Tanner, R.A.; Gange, A.C. The impact of two non-native plant species on native flora performance: Potential implications for habitat restoration. Plant Ecol. 2013, 214, 423–432.
  78. Zubek, S.; Majewska, M.L.; Błaszkowski, J.; Stefanowicz, A.M.; Nobis, M.; Kapusta, P. Invasive plants affect arbuscular mycorrhizal fungi abundance and species richness as well as the performance of native plants grown in invaded soils. Biol. Fertil. Soil 2016, 52, 879–893.
  79. Hale, A.N.; Kalisz, S. Perspectives on allelopathic disruption of plant mutualisms: A framework for individual- and population-level fitness consequences. Plant Ecol. 2012, 213, 1991–2006.
  80. Callaway, R.M.; Cipollini, D.; Barto, K.; Thelen, G.C.; Hallett, S.G.; Prati, D.; Stinson, K.; Klironomos, J. Novel weapons: Invasive plant suppresses fungal mutualists in America but not in its native Europe. Ecology 2008, 89, 1043–1055.
  81. Cantor, A.; Hale, A.; Aaron, J.; Traw, M.B.; Kalisz, S. Low allelochemical concentrations detected in garlic mustard-invaded forest soils inhibit fungal growth and AMF spore germination. Biol. Invasions 2021, 13, 3015–3025.
  82. Chengxu, W.; Mingxing, Z.; Xuhui, C.; Bo, Q. Review on allelopathy of exotic invasive plants. Procedia Engin. 2011, 18, 240–246.
  83. Lockwood, J.L.; Simberloff, D.; McKinney, M.L.; Von Holle, B. How many, and which, plants will invade natural areas. Biol. Invasions 2001, 3, 1–8.
  84. Izhaki, I. Emodin: A secondary metabolite with multiple ecological functions in higher plants. New Phytol. 2002, 155, 205–217.
  85. Langcake, P.; Pryce, R.J. The production of resveratrol by Vitis vinefera and other members of the Vitaceae as a response to infection or injury. Physiol. Plant Pathol. 1976, 9, 77–86.
  86. Langcake, P.; Cornford, C.A.; Pryce, R.J. Identification of pterostilbene as a phytoalexin from Vitis vinefera leaves. Phytochemistry 1979, 18, 1025–1027.
  87. Shi, C.Y.; Ye, Q.B.; Wang, X.H.; Zhang, T.M. Study on the application of Polygonum cuspidatum in “Chinese medince minsterial standards”. Asia Pac. Tradit. Med. 2012, 8, 207–209.
  88. Bourchier, R.S.; Van Hezewijk, B.H. Distribution and potential spread of Japanese knotweed (Polygonum cuspidatum) in Canada relative to climatic thresholds. Invasive Plant Sci. Manag. 2010, 3, 32–39.
More
Information
Subjects: Biology
Contributor MDPI registered users' name will be linked to their SciProfiles pages. To register with us, please refer to https://encyclopedia.pub/register :
View Times: 472
Entry Collection: Environmental Sciences
Revisions: 2 times (View History)
Update Date: 31 Dec 2021
1000/1000