Preferred name: Gymnocoronis spilanthoides
Authority: (D. Don ex Hooker) de Candolle
Taxonomic position: Plantae: Magnoliophyta: Angiospermae: Campanulids: Asterales: Asteraceae: Asteroideae
Other scientific names: Alomia spilanthoides D. Don ex Hooker & Arnott, Gymnocoronis attenuata de Candolle, Gymnocoronis spilanthoides var. attenuata (de Candolle) Baker, Gymnocoronis subcordata de Candolle, Piqueria attenuata (de Candolle) Gardner, Piqueria subcordata (de Candolle) Gardner
Common names in English: Senegal tea, giant green hygro, spade-leaf plant, temple plant, water snowball (US)
view more common names online...
EPPO Categorization: A2 list
EU Categorization: IAS of Union concern
view more categorizations online...
EPPO Code: GYNSP

History of introduction and spread 

Gymnocoronis spilanthoides has a native range within South America (Brazil, Argentina, Paraguay, Uruguay, Bolivia and Peru), mostly centred around Uruguay and Paraguay (King & Robinson, 1987) and is becoming an invasive alien species in several regions of the world. The species is problematic in Australia, New Zealand, Japan, China and Taiwan and has recently naturalized in Italy. 

G. spilanthoides is cultivated in the USA but is not reported as naturalized there (Weed Science Society of America (WSSA), 2012). Records of this species from Central American countries probably refer to another species, Gymnocoronis latifolia (or up to four species depending on the taxonomy) (Turner, 1997). 

The species was reported from India (reputedly the source of introduction to Australia through the aquarium trade) by Parsons & Cuthbertson (2001). There are relatively recent records of naturalization in Japan (in 1995), Taiwan (in 2001) and mainland China (in 2007) (Kodono, 2004; Wang et al., 2010; Wu et al., 2010). Kodono (2004) reports this species as rapidly naturalizing, occurring from Kyushu to central Japan. 

G. spilanthoides was reported as casual in 1988 in Hungary, occurring in the thermal waters of Lake Héviz and ditches near Keszthely (Szabo, 2002; Lukacs et al., 2016). Ardenghi et al. (2016) report two naturalized occurrences in north-western Italy (Lombardia region). The population in Italy stretches along the water body for 519 m, and occupies the whole canal width (1–4 m) (Ardenghi et al., 2016).  In the Netherlands, G. spilanthoides was first identified in an urban waterway in Vleuten in 2019 (EPPO Reporting Service, 2020).   

G. spilanthoides was first reported as a naturalized species in Australia, reported from Taree in New South Wales (NSW) in 1980 (Parsons & Cuthbertson, 2001). It has since spread in NSW and also naturalized in the states of Victoria and Queensland. It has been eradicated from an ornamental pond site in Perth and Margaret River in Western Australia, the only known sites in that state (Hussey et al., 2007). In New Zealand, G. spilanthoides was first recorded as naturalized on the Papakura Stream in South Auckland in 1990 (Timmins & Mackenzie, 1995) and has since been found through much of lowland North Island and two South Island sites, the furthest south being in Canterbury (43.4°S).

Distribution

EPPO Region: France (mainland), Hungary, Italy (mainland), Netherlands
Asia: China (Guangxi, Yunnan, Zhejiang), India, Japan (Honshu, Kyushu), Taiwan
North America: Mexico
South America: Argentina, Bolivia, Brazil, Paraguay, Peru, Uruguay
Oceania: Australia (New South Wales, Queensland, South Australia, Tasmania, Victoria, Western Australia), New Zealand

Plant type 

Emergent amphibious aquatic perennial herb. 

Description 

G. spilanthoides is an emergent perennial herb, either forming upright bushes up to 1.5 m tall, tangled sprawling floating mats or occasionally fully submerged in shallow water. Plants reproduce by seed and vegetative fragmentation, with detached stems rooting at the nodes and thus forming new colonies. Stems are pale green (rarely reddish), either round or six- to eight-angled in cross section, erect or scrambling, up to 1.5 m long and 20 mm across, with hollow internodes, inflated and buoyant. Leaves lanceolate or ovate, opposite, 50–200 mm long 25–75 mm wide, serrate with wavy margins, veins pinnate. Submerged foliage usually entire but with wavy margins, petiolate, 10–70 mm long. Inflorescence glandular hairy, terminal, a cyme of capitula (flowerheads). Capitula discoid, with white (or pinkish) florets, 3.5–4 mm long, subtended by a single row of green involucral bracts, 15– 20 mm across, highly scented and very attractive to butterflies. Fruit is an achene, lacking a pappus, pale brown, slightly curved with prominent ribs, 1.2 mm long and 0.5 mm across (Parsons & Cuthbertson, 2001; New Zealand Plant Conservation Network, 2013; Ardenghi et al., 2016). Seed set variable, with 6–19% of florets producing seed (Vivian-Smith et al., 2005). Adventitious roots commonly developing on the nodes.

General 

Dense emergent beds of G. spilanthoides sprawling over shallow margins of water bodies limit the growth of submerged and other emergent plant species. These beds prevent wind-induced mixing of the water column, causing reductions in dissolved oxygen that may result in anoxia with serious effects on fish and invertebrate species. The plant also increases evapotranspiration, resulting in water loss. These dense plant beds can impede water flow, promoting flooding and also obstructing navigation and recreation (Parsons & Cuthbertson, 2001). 

Habitats

Within its introduced range, G. spilanthoides grows in wetlands, particularly degraded waterways (CRC for Australian Weed Management, 2003) forming marginal clumps on the edge of slow-flowing or still water bodies, also forming dense sprawling floating mats in rivers (including tidally influenced areas) and reservoirs, irrigation channels, ponds, lakes, canals and ditches. It also grows in marshes and swamps, especially where nutrient enriched (CRC for Australian Weed Management, 2003). G. spilanthoides established but did not persist in a rice field in Italy (Ardenghi et al., 2016).

Environmental requirements 

In cooler parts of its introduced range, G. spilanthoides is a summer green, dying back to a perennial rootstock or to submerged plants, even under ice (New Zealand Plant Conservation Network, 2013, P Champion, Pers. Obs. (2016) National Institute of Water and Atmospheric Research Ltd). Burnett (2008) cultivated G. spilanthoides in Hamilton, New Zealand (37.8°S) with water temperature fluctuations between 7 and 23°C. The author then manipulated temperatures either 2, 4 or 6°C above or below ambient temperatures (Burnett et al. 2007) in separate tanks all otherwise experiencing outdoor ambient conditions. Gymnocoronis spilanthoides survived all treatments and all measured growth parameters (stem number, height, percentage cover, biomass) increased with increasing temperature. All treatments apart from +6°C died off to basal rootstocks during winter. The southernmost naturalized G. spilanthoides population was the Waimakariri River margin in Canterbury, New Zealand (43.4°S). Ardenghi et al. (2016) reported Italian sites in the north-west (45.2°N) that experienced hot summers (monthly mean summer temperature approximately 30°C) and relatively cold winters (monthly mean January ≤-1°C). Seed set has been recorded at many New Zealand, Australian and Italian sites (Vivian-Smith et al., 2005; Panetta, 2010; New Zealand Plant Conservation Network, 2013; Ardenghi et al., 2016), with low numbers of seed set. However, germination rates were high over a range of fluctuating temperatures 5/15°C, 10/20–25/15°C or at 25°C (Vivian-Smith et al., 2005; Ardenghi et al., 2016). Seed bank persistence was estimated at more than 16 years until viability was reduced below 1%, but would be much shorter if exposed to daylight (Panetta, 2010). Some field sites are situated on tidally influenced rivers, but tolerance to salinity is unknown. Gymnocoronis spilanthoides has high growth rates under ideal conditions; a shoot growth of 150 mm per week was measured in New South Wales (Parsons & Cuthbertson, 2001). 

Natural enemies 

There are no known natural enemies for G. spilanthoides within the EPPO region. Due to early management intervention in Australia and New Zealand, which has restricted the invasive range of the species, biological control has not been researched (Australian Government, 2016). 

Uses and benefits 

Gymnocoronis spilanthoides is widely sold as an ornamental species within the EPPO region, including internet trade (Brunel, 2009; Ardenghi et al., 2016). The species is also sold/exchanged between aquarists. The Ornamental Aquatic Trade Association (UK based) carried out a survey with its members in August 2016 requesting information on the number and value of G. spilanthoides stock sold at in the calendar year for 2015. Thirty-three members responded to this survey and detailed that a total of 75 700 G. spilanthoides plants were sold in the UK in 2015 with a value of GBP 112 955. 

The species is highly regarded as an ornamental pond plant as its flowers are very attractive to some butterflies, especially monarch butterflies in Australasia and the USA (Speichert & Speichert, 2007), and Kodono (2004) reports the plant is cultivated by butterfly enthusiasts in Japan. Kodono (2004) also reports the plant being promoted in Japan for water purification.

Plants for planting is considered the main pathway for entry into the EPPO region. From this pathway, individual plants can be transferred to suitable habitats through either intentional introductions into the environment or unintentionally through the disposal of aquarium material. 

Consideration can be given to river systems within the EPPO region which are connected to countries outside the EPPO region. It is possible that the use of recreational equipment (e.g. fishing or canoeing gear) could spread the species, particularly as seeds or seedlings, although this is not likely to be significant pathway at present given the rarity of the plant within the EPPO region. However, there are campaigns within the European Union (EU) to raise awareness of the movement of invasive alien plants by this pathway. For example, the ‘Check, Clean and Dry’ campaign in Great Britain highlights the need to inspect and treat recreational material following use.

Effects on plants 

CRC for Australian Weed Management (2003) states that G. spilanthoides threatens biodiversity and causes other environmental damage. Although only in the early stages of establishment, this weed has the potential to seriously degrade Australia’s ecosystems. Because G. spilanthoides grows very quickly, it can rapidly cover water bodies with a floating mat, excluding other plants and the animals that rely on them. Water quality may decline if large amounts of the plant die off and rot under water. 

Environmental and social impact 

G. spilanthoides has been recorded as colonizing a rice field in Italy (Ardenghi et al., 2016) and this could have potential economic impacts relating to crop yields unless managed. The effects of flooding will potentially be made much worse because infestations block drainage channels – although financial figures for this are lacking. Recreational activities (e.g. by preventing access to the water body), irrigation and navigation may also be affected (Parsons & Cuthbertson, 2001).

Manual control has been successful in reducing small infestations of G. spilanthoides, either by hand removal, raking or drainage machinery (Parsons & Cuthbertson, 2001). Plants may be disposed of by drying and burning (CRC for Australian Weed Management, 2003). Care is required not to leave plant fragments that can regenerate into new plants or be spread by water movements to new locations (van Oosterhout, 2010). Re-establishment from seed germination is likely once the plant becomes established in a wetland or aquatic site, requiring follow-up control for many years (Panetta, 2010). In Lake Biwa (Japan) a concerted hand removal programme has resulted in a decrease in abundance and area occupied by G. spilanthoides over 3 years, with eradication anticipated in the near future (Kaneko, 2012). 

Glyphosate has been found to give poor control of G. spilanthoides (Sainty & Jacobs, 2003), with this herbicide poorly translocating into below-ground or underwater parts and in many cases being adsorbed onto the silt coating plants (P. Champion, 2016, pers. obs.). The selective broad-leaf herbicide metsulfuron-methyl does provide good control and has been permitted for minor use on the species in aquatic situations in Australia (van Oosterhout, 2010; New South Wales Department of Primary Industries, 2014) and New Zealand where the majority of field sites of G. spilanthoides have been eradicated using this herbicide (Champion et al., 2002; Champion & Clayton, 2003). Products should be used following the instructions on the label and in line with the relevant plant protection product regulations

Europe (overall): G. spilanthoides was included on the EPPO ‘Alert List’ in 2009. It was removed from this list and transferred to the ‘Observation List’ in 2012. G. spilanthoides was also assessed under an alltaxa horizon scanning exercise designed to help prioritize risk assessments for the ‘most threatening new and emerging invasive alien species’ in Europe (Roy et al., 2015); G. spilanthoides scored 625 representing a high probability of arrival, establishment, spread and threat to biodiversity and associated ecosystem services across the EU within the next 10 years. In 2016, G. spilanthoides was identified as a priority for risk assessment within the requirements of Regulation 1143/2014 (Branquart et al., 2016; Tanner et al., 2017). A subsequent pest risk analysis concluded that G. spilanthoides had a high phytosanitary risk to the endangered area (EPPO, 2017) and was added to the EPPO A2 List of pests recommended for regulation. In 2019, G. spilanthoides was included on the (EU) list of Union concern (EU Regulation 1143/2014) 

G. spilanthoides is designated as an invasive alien species according to the Invasive Alien Species Act of Japan (Muranaka et al., 2005). 

In New Zealand, G. spilanthoides is listed on the National Plant Pest Accord prohibiting it from sale and commercial propagation and distribution, and it is declared an unwanted organism under the Biosecurity Act 1993 (Hicks, 2001). It is subjected to eradication programmes by regional councils throughout its New Zealand range (Champion et al., 2014). It is listed as an Environmental Weed by Howell (2008). 

In Australia, G. spilanthoides is on the Federal Alert List for Environmental Weeds, a list of 28 non-native plants that threaten biodiversity and cause other environmental damage. Although only in the early stages of establishment, these weeds have the potential to seriously degrade Australia’s ecosystems. It is subject to statutory management in most Australian states including New South Wales, Queensland, South Australia, Western Australia, Tasmania and Lord Howe Island (Parsons & Cuthbertson, 2001). Csurhes & Edwards (1998) evaluated this species as a potential environmental weed, with a low probability of achieving eradication. 

G. spilanthoides is not on the Federal or any state Noxious Weed list (USDA National Resources Conservation Service 2016).

Ardenghi NMG, Barcheri G, Ballerini C, Cauzzi P & Guzzon F (2016) Gymnocoronis spilanthoides (Asteraceae, Eupatorieae), a new naturalized and potentially invasive aquatic alien in S Europe. Willdenowia 46, 265–273. 

Australian Government (2016) Weeds in Australia: Gymnocoronis spilanthoides. http://www.environment.gov.au/cgi-bin/biodiversity/invasive/weeds/weeddetails.pl?taxon_id=12850 [accessed on 9 September 2016] 

Branquart E, Brundu G, Buholzer S, Ehret P, Fried G, Starfinger U et al. (2016) A prioritization process for invasive alien plant species compliant with Regulation (EU) No. 1143/2014. EPPO Bulletin 46, 603–617. 

Burnett DA (2008) Assessment of potentially invasive aquatic plants under modified temperature regimes. Auckland University, Unpublished PhD thesis. 224 pp. 

Burnett DA, Champion PD, Clayton JS & Ogden J (2007) A system for investigation of the temperature responses of emergent aquatic plants. Aquatic Botany 86, 187–190.

Brunel S (2009) Pathway analysis: aquatic plants imported in 10 EPPO countries. European and Mediterranean Plant Protection Organization Bulletin 39, 201–213. 

Champion PD & Clayton JS (2003) The evaluation and management of aquatic weeds in New Zealand. In Plant Invasions: Ecological Threats and Management Solutions (Eds Child L, Brock JH, Brundu G, Prach K, Pysek P, Wade PM & Williamson M), pp. 429–434. Backhuys Publishing, Leiden (NL). 

Champion PD, Rowe D & Clayton JS (2002) Lake Manager Handbook: Alien Invaders. https://www.mfe.govt.nz/sites/default/file s/lm-alien-invaders-jun02.pdf [accessed on 8 September 2016] 

Champion PD, de Winton MD & Clayton JS (2014) A risk assessment based proactive management strategy for aquatic weeds in New Zealand. Management of Biological Invasions 5, 233–240. 

CRC for Australian Weed Management (2003) Senegal tea plant – Gymnocoronis spilanthoides weed management guide. http://www.environment.gov.au/biodiversity/invasive/weeds/publications/guidelines/alert/pubs/g-spilanthoides.pdf [accessed on 3 September 2016] 

Csurhes S & Edwards R (1998) National weeds program: potential environmental weeds in Australia. Candidate species for preventative control. http://www.environment.gov.au/biodiversity/invasive/weeds/publications/books/pubs/potential.pdf [accessed on 5 September 2016] 

EPPO (2020) EPPO Reporting Service 2020/059 

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Hicks G (2001) Department of conservation unwanted organism declaration: Gymnocoronis spilanthoides 31 July 2001. 

Howell CJ (2008) Consolidated List of Environmental Weeds in New Zealand. Science & Technical Publication, Department of Conservation. http://www.doc.govt.nz/documents/science-and-technical/drds292.pdf [accessed on 8 September 2016] 

Hussey BMJ, Keighery GJ, Dodd J, Lloyd SG & Cousens RD (2007) Western Weeds, A Guide to the Weeds of Western Australia, 2nd edn. The Weeds Society of Western Australia (Inc.). 

Kaneko Y (2012) Invasive alien plant species in the shore areas surrounding Lake Biwa. In Lake Biwa: Interactions Between Nature and People (Eds Kawanabe H, Nishino M & Maehata M), pp. 485– 490. Springer, Dordrecht (NL), Heidelberg (DE), New York, NY (US), London (UK). 

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Kodono Y (2004) Alien aquatic plants naturalized in Japan: history and present status. Global Environmental Research 8, 163–169. 

Lukacs BA, Mesterhazy A, Vidéki R & Kiraly G (2016) Alien aquatic vascular plants in Hungary (Pannonian ecoregion): historical aspects, data set and trends. Plant Biosystems 148, 388–395. 

Muranaka T, Ishii J, Miyawaki S & Washitani I (2005) Vascular plants to be designated Invasive Alien Species according to the Invasive Alien Species Act of Japan. Japanese Journal of Conservation Ecology 10, 19–33 (in Japanese). 

New South Wales Department of Primary Industries (2014) Senegal tea plant (Gymnocoronis spilanthoides) http://weeds.dpi.nsw.gov.au/ Weeds/Details/169 [accessed on 3 September 2016] 

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Panetta FD (2010) Seed persistence of the invasive aquatic plant, Gymnocoronis spilanthoides (Asteraceae). Australian Journal of Botany 57, 670–674 

Parsons WT & Cuthbertson EG (2001) Noxious Weeds of Australia. 698 pp. CSIRO Publishing, Collingwood, Vic. (AU). 

Roy HE, Adriaens T, Aldridge DC, Bacher S, Bishop JDD, Blackburn TM et al. (2015) Invasive Alien Species – Prioritising prevention efforts through horizon scanning ENV.B.2/ETU/2014/0016. European Commission. 

Sainty GR & Jacobs SWL (2003) Waterplants in Australia, 4th edn, 416 pp. Sainty & Associates Pty Ltd, Potts Point, NSW (AU). 

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Tanner R, Branquart E, Brundu G, Buholzer S, Chapman D, Ehret P et al. (2017) The prioritisation of a short list of alien plants for risk analysis within the framework of the regulation (EU) No. 1143/2014. NeoBiota 35, 87–118. 

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This datasheet is an output of DG Environment, LIFE funding under the project LIFE15 PRE-FR 001: Mitigating the threat of invasive alien plants in the EU through pest risk analysis to support the EU Regulation 1143/2014. The datasheet was produced following an expert working group that risk analysed G. spilanthoides for the EPPO region in October 2016. The composition of the expert working group was: D. Chapman (Centre for Ecology and Hydrology, UK), A. Petroeschevsky (Australia), D. Lieurance (University of Florida, US), P. Champion (National Institute of Water and Atmospheric Research, NZ), A. Hussner (University of Dusseldorf, DE), J. van Valkenburg (National Plant Protection Organization, NL), R. Tanner (EPPO)

EPPO (2024) Gymnocoronis spilanthoides. EPPO datasheets on pests recommended for regulation. https://gd.eppo.int (accessed 2024-12-21)

This datasheet was first published in the EPPO Bulletin in 2017 and is now maintained in an electronic format in the EPPO Global Database. The sections on 'Identity' and 'Geographical distribution' are automatically updated from the database. For other sections, the date of last revision is indicated on the right.

EPPO (2017) Gymnocoronis spilanthoides. Datasheets on pests recommended for regulation. EPPO Bulletin 47(3), 544-548. https://doi.org/10.1111/epp.12430