Hemimysis anomala

Pictures

Picture	Title	Caption	Copyright
Title Adult Caption Hemimysis anomala (bloody-red shrimp); adult. Copyright ©Matthieu Dautriourt/via wikipedia - CC BY-SA 4.0	Adult	Hemimysis anomala (bloody-red shrimp); adult.	©Matthieu Dautriourt/via wikipedia - CC BY-SA 4.0
Title Adult Caption Hemimysis anomala (bloody-red shrimp); adult. Copyright Public Domain - Released by NOAA-United States Great Lakes Environmental Research Laboratory (GLERL). Original image by Steve Pothoven, NOAA	Adult	Hemimysis anomala (bloody-red shrimp); adult.	Public Domain - Released by NOAA-United States Great Lakes Environmental Research Laboratory (GLERL). Original image by Steve Pothoven, NOAA
Title Adult Caption Hemimysis anomala (bloody-red shrimp); adult. Copyright Public Domain - Released by NOAA-United States Great Lakes Environmental Research Laboratory (GLERL). Original image by Steve Pothoven, NOAA	Adult	Hemimysis anomala (bloody-red shrimp); adult.	Public Domain - Released by NOAA-United States Great Lakes Environmental Research Laboratory (GLERL). Original image by Steve Pothoven, NOAA
Title Adults Caption Hemimysis anomala (bloody-red shrimp); adults. Copyright Public Domain - Released by NOAA-United States Great Lakes Environmental Research Laboratory (GLERL). Original image by Steve Pothoven, NOAA	Adults	Hemimysis anomala (bloody-red shrimp); adults.	Public Domain - Released by NOAA-United States Great Lakes Environmental Research Laboratory (GLERL). Original image by Steve Pothoven, NOAA

Identity

Preferred Scientific Name

• Hemimysis anomala G.O.Sars, 1907

International Common Names

• English: bloody-red shrimp

Local Common Names

• Netherlands: Bloedrode Kaspische aasgarnaal; Kaspische aasgarnaal
• Ukraine: Mizida anomal'na

Summary of Invasiveness

H. anomala is a small mysid shrimp native to the Ponto-Caspian region. In the 1950s and 1960s it was used to stock reservoirs in Eastern Europe to promote fish production (Gasiunas, 1968; Grigorovich et al., 2002). Following successful population establishment in these reservoirs, H. anomala was passively transported to the Baltic Sea, where the first accidentally introduced invasive populations were reported in the Curonian Lagoon off the Lithuanian coast in 1962 (Gasiunas, 1964). Further range expansion has been facilitated by a wide salinity tolerance (Ellis and MacIsaac, 2009), which has enabled the mysid to be transported over great distances in ballast water. It has now been observed in numerous countries across mainland Europe, in the United Kingdom and in North America and Canada. The mysid’s euryhalinity has allowed invasive populations to become established in a wide variety of habitat types, including coastal waters, lagoons, estuaries, rivers, canals and reservoirs. It can reach high population densities in newly invaded habitats (Holdich et al., 2005; Pothoven et al., 2007; Wittmann, 2007) and acts as a top-down regulator of the plankton community; it can therefore have a significant impact on the ecology of a receiving environment (Ketelaars et al., 1999). No methods have been developed to control invasive mysid populations.

Taxonomic Tree

• Domain: Eukaryota
•     Kingdom: Metazoa
•         Phylum: Arthropoda
•             Subphylum: Crustacea
•                 Class: Malacostraca
•                     Subclass: Eumalacostraca
•                         Order: Mysidacea
•                             Family: Mysidae
•                                 Genus: Hemimysis
•                                     Species: Hemimysis anomala

Notes on Taxonomy and Nomenclature

The order Mysidacea comprises at least 780 species (Borcherding et al., 2006) and according to some sources, more than 1000 species (Meland, 2009). Of these, the vast majority are marine species, with only ~25 inhabiting freshwater and brackish water environments (Mauchline, 1980). The genus Hemimysis was first described by Sars in 1869 and comprises six species, including the brackish and freshwater inhabitant Hemimysis anomala, which Sars described in 1907.

Description

H. anomala is a relatively small mysid shrimp. The species usually has a distinctive red colouration in live specimens due to the presence of chromatophores; individuals lacking this colouration are ivory yellow to almost transparent (Ketelaars et al., 1999; Pothoven et al., 2007). The species has large spherical eyes with a notch in the dorsal margin. Sex can be determined by consulting the 4th pleopods: in males, these are elongated and modified for copulation, whereas females have rudimentary pleopods (Pothoven et al., 2007); adult females also have a brood pouch. Females are the larger sex, reaching 16.5 mm in marine habitats (Bacescu, 1940), whilst males achieve a maximum length of 11 mm (Komarova, 1991). Individuals from freshwater ecosystems are shorter, for example Pothoven et al. (2007) recorded a mean length of 7.03 mm in females collected from the Great Lakes in November, and similarly the mean length of females collected by Ketelaars et al. (1999) from a Dutch reservoir in September was 8.4 mm (minimum 6.5 mm; maximum 12.5 mm). Males were on average < 0.5 mm shorter in both studies. Ketelaars et al. (1999) noted the body length of juveniles as ranging from 1.4 mm to 9.9 mm. For further description of morphological characteristics, see section ‘Similarities to Other Species/Conditions’.

Distribution

H. anomala is of Ponto-Caspian origin, and is regarded as native only to freshened parts of the Black Sea (Pothoven et al., 2007) and the estuaries and lower reaches < 60 km upstream) of rivers draining into the Black Sea, Sea of Azov and the eastern Caspian Sea (Audzijonyte et al., 2008, and references therein). The species’ anthropogenic range expansion began in the 1950s and 1960s, when it was successfully inoculated into reservoirs in Eastern Europe to promote fish production (Gasiunas, 1968). These intentional introductions gave H. anomala downstream access to the Baltic Sea. From the Baltic and also from its native range, the species has spread west across Europe, this range expansion being facilitated by ballast water exchange by international vessels. It has recently reached both the United Kingdom and North America as a result of leisure craft activities and international shipping.

Distribution Table

The distribution in this summary table is based on all the information available. When several references are cited, they may give conflicting information on the status. Further details may be available for individual references in the Distribution Table Details section which can be selected by going to Generate Report.

History of Introduction and Spread

H. anomala is one of many Ponto-Caspian species to have undergone considerable range expansion in recent decades, beginning with its deliberate introduction into impounded waters in Lithuania, Ukraine and Moldova in the 1950s and 1960s to promote fish production (Zhuravel, 1960; Gasiunas, 1964; Grigorovich et al., 2002). From the populations introduced into Lithuania, H. anomala spread to the Baltic Sea through passive downstream transport in rivers (Audzijonyte et al., 2008). It was observed in the Curonian Lagoon, connected to the Baltic Sea off the coast of Lithuania, in 1962 (Gasiunas, 1964), and established populations have since been recorded in the Baltic in the coastal waters of Finland in 1992 (Salemaa and Hietalahti, 1993), Sweden in 1995 (Kautsky, 1996) and Poland in 2002 (Janas and Wysocki, 2005). Baltic populations have spread to the Rhine delta in the Netherlands and have progressed upstream into the German Rhine, facilitated by international shipping (Audzijonyte et al., 2008). H. anomala was first observed in the Netherlands in 1997, inhabiting a reservoir in the Rhine basin (Ketelaars et al., 1999), and the mysid was also first recorded in the German Rhine in this year (Schleuter et al., 1998).

Introductions

Risk of Introduction

Deliberate introductions of H. anomala largely ceased in the 1980s, as awareness of the detrimental ecological impacts of such activity increased (Rieman and Falter, 1981; Wittmann, 2007). Furthermore, many fish species are unable to exploit H. anomala as prey (Ketelaars et al., 1999), and H. anomala may outcompete planktivorous fish for zooplankton food resources (Spencer et al., 1991); introductions are therefore potentially counterproductive. Despite the cessation of intentional releases, accidental introductions of H. anomala and other aquatic invasive species (AIS) continue to be reported. Current legislation enacted to prevent these accidental introductions does not appear to be effective, specifically that related to ballast water exchange (Ellis and MacIsaac, 2009). Therefore, further introductions of H. anomala and other AIS into international ports through ballast water exchange is anticipated (Pothoven et al., 2007). The species can only reproduce sexually (Mauchline, 1980), and therefore a female carrying fertilized eggs or a combination of male and female individuals must be introduced for population growth to occur. In addition, certain environmental criteria must be fulfilled for introduced individuals to thrive in a newly colonized habitat. However H. anomala can tolerate a wide range of environmental conditions, and in practice there appear to be few barriers preventing population establishment (Pienimäki and Leppäkoski, 2004). H. anomala has only a very limited ability to swim against a current (Stubbington, 2006; Wittmann and Ariani, 2009), and this may limit its upstream range extension following an initial introduction. However, its distribution in countries including England indicates that H. anomala has some capacity to migrate upstream through slow flowing habitat (Stubbington et al., 2008). Based on records of its spread to date, H. anomala is considered to have the capacity for more rapid range expansion than any other Ponto-Caspian AIS (Wittmann, 2006; Wittmann and Ariani, 2009). Pienimäki and Leppäkoski (2004), for example, predict that H. anomala will arrive in the Finnish Lake District in the near future.

Habitat

In its native range, H. anomala is a deep water species that avoids exposure to daylight (Lindström, 2000). In the Black Sea, it is commonly found at depths of 6 - 10 m, although it has been observed at depths of 20 m in the Black Sea, 30 m in the Caspian Sea (Bacescu, 1954), and as deep as 50 m in the Dneiper River (Zhuravel, 1960). Many invasive populations are also found in deep water, in both sublittoral coastal areas and inland habitats. Salemaa and Hietalahti (1993), for example, observed swarms at depths of 2 - 12 m along the Baltic shoreline, and Verslycke et al. (2000) collected individuals from a depth of 13 m in a brackish water pond. In deep water, the species undergoes diurnal vertical migrations, entailing the extension of vertical distribution into shallower water after dark (Mauchline, 1980; Salemaa and Hietalahti, 1993; Ketelaars et al., 1999).

Habitat List

Biology and Ecology

Genetics

To date, only one study has considered the genetics of H. anomala (i.e. Audzijonyte et al., 2008), and this study only sequenced a fragment of a single mitochrondrial gene. Audzijonyte et al. (2008) analysed 130 individuals from across H. anomala’s entire range (including native and invasive populations) and differentiated between nine haplotypes in three distinct clusters. Mean divergence among the three clusters was 0.9-1.5%, where 0.5% divergence is considered to be relative genetic uniformity and 5% divergence indicates deep genetic subdivisions (Audzijonyte et al., 2008).

Reproductive Biology

Ioffe (1973) studied the lifecycle of a H. anomala population introduced into the Ukrainian Zaporozhie reservoir and noted the start of the breeding season in April, with the first ovigerous females being observed as water temperature reached 8-9°C. At 11-12°C, neonates were observed in the marsupium, the first young were released in late May, and reproduction continued until October. Other studies have noted a similar breeding season, for example Salemaa and Hietalahti (1993), studying an invasive population in the coastal waters of the Baltic, observed females with fully developed ovocytes as early as April, with breeding females being present until the end of October. Pothoven et al. (2007) noted that females carrying young were still present in Lake Michigan in November, when water temperature was 8°C.

Ioffe (1973) observed reproduction in females of the first generation of the year 45 days after release, with the second and third generations developing even more rapidly and reaching maturity within one month. In total, four generations were produced in one year, the highest recorded in any study (Ioffe, 1973). Borcherding et al. (2006) observed only two generations (in April/May and September) in an invasive population in a gravel pit in Germany, but considered a third generation, released during the summer months, to be likely. Similarly, Mordukhai-Boltovskoi (1970) noted that most female H. anomala produce at least two broods per year. Ioffe (1973) recorded a clutch size of between 14 and 66 eggs per female in the Zaporozhie reservoir, depending on female size and season. Other studies have considered the number of young rather than eggs: Ketelaars et al. (1999) recorded a mean brood size of 13 young per female in a Dutch reservoir; Borcherding et al. (2006) noted a mean brood size of 29 young in April and 20 young in September in the German gravel-pit population; and Pothoven et al. (2007) found that clutch size varied between 2-17 young in the Lake Michigan basin.

Factors affecting fecundity include water temperature, trophic status (in lakes) and female length (Ketelaars et al., 1999), the latter being influenced by salinity, with larger individuals found in saltwater compared with freshwater (Bacescu, 1969). Invasive populations in relatively warm, brackish waters therefore have the potential for the most rapid population expansion.

Climate

Latitude/Altitude Ranges

Air Temperature

Water Tolerances

Natural enemies

Notes on Natural Enemies

Fish species vary in their ability to prey upon H. anomala, due to the latter remaining hidden during daylight hours. Certain species have been shown to consume considerable numbers of H. anomala, in particular adult perch (Perca fluviatilis), which is native throughout the mysid’s current European range including the UK. Ketelaars et al. (1999) analyzed the stomach contents of five perch and found three to be ‘completely stuffed’ with them, and Borcherding et al. (2006) also noted that perch preyed heavily on the mysid, leading to above average growth in young-of-the-year individuals. This predation pressure, however, appears insufficient to have a significant impact on H. anomala abundance, with both Ketelaars et al. (1999) and Borcherding et al. (2006) reporting high density mysid populations.

Means of Movement and Dispersal

Natural Dispersal (Non-Biotic)

The natural dispersal capacity of H. anomala is limited by its poor swimming ability and therefore its restricted capacity for upstream migration. As such, its native range is limited to the lowest reaches of rivers draining into the Black, Azov and Caspian Seas. Following an accidental introduction, however, it can spread downstream rapidly and over great distances by being passively transported by the current. Wittmann and Ariani (2009), for example, attribute the sudden appearance of H. anomala at sites spanning > 250 km on the Rhône River in southeastern France to passive downstream drift. Dispersal has also been facilitated by man-made waterways that link previously unconnected river basins, most notably the Rhine-Main-Danube Canal, which links the Black Sea and the vast Danube River basin with the German Rhine and thence the North Sea. The rate of dispersal through canal networks is presumably reduced compared with downstream drift since it is largely dependent on active swimming, however, actual rates cannot be determined from records of first occurrences due to inconsistent sampling efforts.

H. anomala is not believed to be dispersed by biotic vectors such as water birds.

The primary means by which H. anomala has expanded its range is international shipping and associated ballast water exchange. Genetic analysis has indicated that international shipping has facilitated dispersal west across mainland Europe from both the Danube delta and the Baltic Sea to the Rhine delta in the Netherlands, and thence to the United Kingdom, Canada and North America (Audzijonyte et al., 2008). The nature of this dispersal mechanism means that the rate of spread may be sporadic, but equally, vast distances can be traversed extremely rapidly; the first observations in North America, for example, occurred only two years after the initial reports from the UK (Holdich et al., 2005; Pothoven et al., 2007).

In the 1950s and 1960s, H. anomala was one of several Ponto-Caspian endemics used to enhance fish production in impounded waters in Eastern Europe (Lithuania, Moldova and Ukraine) (Zhuravel, 1960; Gasiunas, 1964; Grigorovich et al., 2002), and these introductions unintentionally facilitated further spread. However, since the 1980s, awareness of the detrimental ecological impacts of such introductions has increased (Rieman and Falter, 1981; Wittmann, 2007) and there are no reports of intentional releases in recent decades.

Pathway Causes

Pathway Vectors

Impact Summary

Impact

Invasive H. anomala populations can reach high densities in suitable habitats (Ketelaars et al., 1999; Borcherding et al., 2006; Pothoven et al., 2007) and as such are likely to have a considerable impact on the receiving ecosystem. However, the mysid has proved able to establish populations in a range of habitats across a large geographical area, and variation in the climatic, hydrological and ecological conditions of the receiving ecosystems means that the effects of an invasive population can also be highly variable (Pienimäki and Leppäkoski, 2004).

Economic Impact

The economic impacts of invasive H. anomala populations have to date proved relatively minor and localized, and may be either positive or negative.

Environmental Impact

H. anomala has a high feeding rate, can achieve high population densities and consumes a wide variety of food types, including phytoplankton and detritus (Ketelaars et al., 1999; Borcherding et al., 2006). An invasive population can therefore alter the physical environment by increasing light penetration into the water column, thus promoting photosynthesis and increasing plant productivity. Irvine et al. (1993), for example, linked an increase in submerged macrophyte growth in a shallow brackish lake to an increased abundance of the mysid Neomysis integer. Similarly, Stubbington et al. (2008) noted a proliferation of Elodea sp. in a freshwater regatta lake following the establishment of an invasive H. anomala population.

H. anomala acts as a top-down regulator of the plankton community and can therefore alter community structure at multiple trophic levels, potentially lowering the number of trophic levels and thus reducing ecosystem stability (Salemaa and Hietalahti, 1993; Ketelaars et al., 1999). H. anomala has been shown to have a detrimental impact on certain components of the zooplankton community through predation, for example Ketelaars et al. (1999) noted a decline in the Cladocera, Ostracoda and Rotifera following the establishment of an invasive H. anomala population, whilst Borcherding et al. (2006) found that the mysid preyed heavily on the Copepoda. H. anomala may outcompete species with similar dietary requirements for these prey, for example Verslycke et al. (2000) noted a decline in the abundance of the mysid Neomysis integer following the establishment of a H. anomala population in a brackish water pond. Planktivorous fish, in particular the juveniles of species such as perch and roach (Rutilus rutilus), may also face increased competition for food resources, leading to population declines with potential consequences at higher trophic levels (Spencer et al., 1991). Conversely, H. anomala is also a high quality prey species for fish able to exploit its diurnal migrations, in particular adult Perch (Ketelaars et al., 1999; Borcherding et al., 2006), and such species may therefore become more abundant.

The establishment of an invasive H. anomala population has not, to date, been proved responsible for declines in any particular species. This may, however, reflect that research in this area has only recently begun, rather than an actual absence of such declines.

Social Impact

H. anomala has established populations in habitats in which recreational fishing occurs, however, an invasive mysid population can have unpredictable consequences for fish populations (Spencer et al., 1991; Borcherding et al., 2006). H. anomala can potentially outcompete planktivorous fish species (particularly juveniles) for zooplankton food resources, but to date, no reports of detrimental impacts on recreationally important fish populations have been published. In fact, fishermen have tentatively welcomed H. anomala to the North American Great Lakes as a potentially important prey species for the alewife(Alosa pseudoharengus) (USGS, 2008). It may be too early to assess the long-term impacts of recently established H. anomala populations on existing fish populations of recreational importance.

Risk and Impact Factors

• Proved invasive outside its native range
• Abundant in its native range
• Highly adaptable to different environments
• Is a habitat generalist
• Tolerant of shade
• Capable of securing and ingesting a wide range of food
• Fast growing
• Has high reproductive potential
• Gregarious

• Altered trophic level
• Ecosystem change/ habitat alteration
• Reduced native biodiversity
• Threat to/ loss of native species

• Competition - monopolizing resources
• Herbivory/grazing/browsing
• Predation
• Rapid growth

• Highly likely to be transported internationally accidentally
• Highly likely to be transported internationally illegally
• Difficult to identify/detect in the field
• Difficult/costly to control

Uses

Intentional introductions of H. anomala into reservoirs to enhance fish production had ceased by the 1980s, due to the recognition that such activity could have detrimental ecological consequences in the receiving ecosystems (Rieman and Falter, 1981). As such, H. anomala is no longer a species of economic value.

As discussed in the ‘Social Impact’ section, H. anomala can, under certain circumstances, boost fish productivity and this can have a positive impact on recreational fishing (USGS, 2008). However, the mysid is not known to have been deliberately exploited to enhance recreational fishing.

H. anomala is not used in the provision of any environmental services.

Uses List

Animal feed, fodder, forage

• Fishmeal

Detection and Inspection

A variety of techniques have been used, intentionally and unintentionally, to observe and collect specimens from invasive H. anomala populations, including diving (Salemaa and Hietalahti, 1993; Dumont, 2006), vertical plankton hauls (Ketelaars et al., 1999), pond/dip nets (Verslycke et al., 2000; Pothoven et al., 2007), baited bottle traps (Borcherding et al., 2006; Wittmann, 2007), and searching by torchlight (Holdich et al., 2005; Stubbington et al., 2008). All techniques appear to be effective for initial surveys of the habitats in which they have been employed, with the mysid’s coloration, size and reflective eyes aiding preliminary identification in the field. Not all techniques are suitable in all habitats; however, for example searching by torchlight is only effective in shallow water. In all cases, collection and subsequent identification in the laboratory is necessary to confirm the specimens as H. anomala. Mysids can be identified to genus using Mauchline (1980); further information regarding identification to species level is provided in the ‘Similarities to Other Species/Conditions’ section.

Similarities to Other Species/Conditions

H. anomala may be the sole representative of the Mysidacea in an invaded region (e.g. Holdich et al., 2005), in which case confusion with other species is unlikely. If other mysids are also present, the red coloration of H. anomala can be a useful identification aid in field situations. A UK identification guide to invasive freshwater shrimps and isopods includes species present in the UK and others that are invasive across Europe (Dobson, 2012). 

Prevention and Control

Due to the variable regulations around (de)registration of pesticides, your national list of registered pesticides or relevant authority should be consulted to determine which products are legally allowed for use in your country when considering chemical control. Pesticides should always be used in a lawful manner, consistent with the product's label.

SPS Measures

In 2004, the International Maritime Organisation adopted the International Convention for the Control and Management of Ships' Ballast Water and Sediments, which will enter into force 12 months after it has been ratified by 30 States, representing 35% of world merchant shipping tonnage. However, to date (April 2009), only 18 States had ratified the convention, representing 15.36% of world merchant shipping tonnage (International Maritime Organization, 2009). Until the convention is ratified, some countries are following voluntary guidelines intended to prevent the spread of invasive species (Johnson, 2008). Particularly strict regulations controlling ballast water exchange were implemented in 1993 to protect the North American Great Lakes from further invasions (United States Coast Guard, 1993), however, even these measures do not appear to have succeeded in slowing the invasion rate (Ellis and MacIsaac, 2009).

Public Awareness

Efforts to raise public awareness of H. anomala are regionally variable and are most notable in the North American Great Lakes, being coordinated by the National Centre for Research on Aquatic Invasive Species (NCRAIS) and affiliated organizations. NCRAIS provide information enabling the public to recognize H. anomala and provide a mechanism for reporting sightings through the ‘Hemimysis anomala Survey & Monitoring Network’ (NCRAIS, 2009). Elsewhere, little has been done to raise public awareness of H. anomala.

Eradication

No records of any attempts to eradicate H. anomala have been published to date.

Containment/zoning

No attempts to contain invasive populations of H. anomala have been reported.

At present, no method has been developed to remove an invasive mysid populations that has become established.

Biological Control

In some habitats, high densities of planktivorous fish can potentially limit the population expansion of H. anomala through predation (Pothoven et al., 2007). However, to date, this predation has not been exploited to develop biological control strategies for H. anomala or any other mysids.

Gaps in Knowledge/Research Needs

No control measures currently exist for established populations of invasive zooplankters such as H. anomala; extensive research is therefore required in this area and should be prioritized. Further research is also required regarding the impact of an invasive H. anomala population on the receiving ecosystem, for example to substantiate claims that the mysid may reduce the abundance of toxic blue-green algae, and may encourage the growth of submerged macrophytes (Stubbington et al., 2008). Determining those populations likely to have particularly pronounced detrimental impacts on the receiving environment will allow prioritization of the implementation of any newly developed control measures.

References

Audzijonyte A; Wittmann KJ; Väinölä R, 2008. Tracing recent invasions of the Ponto-Caspian mysid shrimp Hemimysis anomala across Europe and to North America with mitochondrial DNA. Diversity and Distributions, 14(2):179-186. http://www.blackwell-synergy.com/loi/ddi

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Bacescu M, 1969. Order Mysidacea. In: Nauk. Dumka, Kiyev [ed. by Key to Black Sea and Sea of Azov fauna], 363-381.

Bales M; Moss B; Phillips G; Irvine K; Stansfield J, 1993. The changing ecosystem of a shallow, brackish lake, Hickling Broad, Norfolk, UK. II. Long-term trends in water chemistry and ecology and their implications for restoration of the lake. Freshwater Biology, 29(1):141-165.

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Dobson M, 2012. Identifying Invasive Freshwater Shrimps and Isopods., UK: Freshwater Biological Association, 30 pp. https://secure.fera.defra.gov.uk/nonnativespecies/news/index.cfm?id=77

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Ellis S; MacIsaac HJ, 2009. Salinity tolerance of Great Lakes invaders. Freshwater Biology, 54(1):77-89. http://www.blackwell-synergy.com/loi/fwb

Gasiunas II, 1964. Acclimatization of forage crustaceans into the Kaunas hydropower plant reservoir and possibility of their migration into other waters of Lithuania. Trudy Akademii Nauk Litovskoi SSR, Seriya B, 1((30)):79-85.

Gasiunas II, 1968. [English title not available]. (Akklimatizatsiya mizidii Hemimysis anomala Sars v vodokhranilishche Kaunasskoi GES) Trudy Akademii Nauk Litovskoi SSR,Seriya B, 3:71-73.

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Janas U; Wysocki P, 2005. Hemimysis anomala G. Sars, 1907 (Crustacea, Mysidacea) - first record in the Gulf of Gdansk. Oceanologia, 47:405-408.

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Kelleher B; Velde GDer; Wittmann KJ; Faasse MA; Bij Vaate Ade, 1999. Current status of the freshwater Mysidae in the Netherlands: with records of Limnomysis benedeni (Czerniavsky 1882), a pontocaspian species in Dutch Rhine branches. Bulletin Zoölogisch Museum Universiteit Van Amsterdam, 16:89-94.

Kestrup AM; Ricciardi A, 2008. Occurrence of the Ponto-Caspian mysid shrimp Hemimysis anomala (Crustacea, Mysida) in the St. Lawrence River. Aquatic Invasions, 3(4):461-464. http://www.aquaticinvasions.ru/2008/AI_2008_3_4_Kestrup_Ricciardi.pdf

Ketelaars HAM; Lambregts-van de Clundert FE; Carpentier CJ; Wagenvoort AJ; Hoogenboezem W, 1999. Ecological effects of the mass occurrence of the Ponto-Caspian invader, Hemimysis anomala G.O. Sars, 1907 (Crustacea: Mysidacea), in a freshwater storage reservoir in the Netherlands, with notes on its autecology and new records. Hydrobiologia, 394:233-248.

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Stubbington R; Terrell-Nield C; Harding P, 2008. The first occurrence of the Ponto-Caspian invader, Hemimysis anomala G. Sars, 1907 (Mysidacea) in the U.K. Crustaceana, 81((1)):43-55.

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Wittmann KJ; Ariani AP, 2009. Reappraisal and range extension of non-indigenous Mysidae (Crustacea, Mysida) in continental and coastal waters of eastern France. Biological Invasions, 11(2):401-407. http://www.springerlink.com/content/kx20151n83677237/?p=d48c11cd995e4d45b8e6c4892ae212b9&pi=22

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Distribution References

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Horecky J, Šporka F, Stuchlík E, 2005. First record of Hemimysis anomala Sars (Crustacea: Mysidacea) from the Czech stretch of the Elbe river (Czech Republic). Lauterbornia. 89-91.

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Kelleher B, Velde G Der, Wittmann K J, Faasse M A, Bij Vaate A de, 1999. Current status of the freshwater Mysidae in the Netherlands: with records of Limnomysis benedeni (Czerniavsky 1882), a pontocaspian species in Dutch Rhine branches. Bulletin Zoölogisch Museum Universiteit Van Amsterdam. 89-94.

Kestrup Ǻ M, Ricciardi A, 2008. Occurrence of the Ponto-Caspian mysid shrimp Hemimysis anomala (Crustacea, Mysida) in the St. Lawrence River. Aquatic Invasions. 3 (4), 461-464. http://www.aquaticinvasions.ru/2008/AI_2008_3_4_Kestrup_Ricciardi.pdf DOI:10.3391/ai.2008.3.4.18

Ketelaars H A M, Lambregts-van de Clundert F E, Carpentier C J, Wagenvoort A J, Hoogenboezem W, 1999. Ecological effects of the mass occurrence of the Ponto-Caspian invader, Hemimysis anomala G.O. Sars, 1907 (Crustacea: Mysidacea), in a freshwater storage reservoir in the Netherlands, with notes on its autecology and new records. Hydrobiologia. 233-248. DOI:10.1023/A:1003619631920

Kipp R N, Ricciardi A, 2007. Hemimysis anomala factsheet. In: Hemimysis anomala factsheet, Michigan, USA: National Center for Research on Aquatic Invasive Species. http://www.glerl.noaa.gov/hemimysis/hemi_sci_factsheet.html\http://www.glerl.noaa.gov/res/Programs/ncrais/hemimysis/docs/hemi_sci_factsheet.pdf

Leppäkoski E, Olenin S, 2000. Non-native species and rates of spread: lessons from the brackish Baltic Sea. Biological Invasions. 151-163.

Minchin D, Holmes J M C, 2008. The Ponto-Caspian mysid, Hemimysis anomala G.O. Sars 1907 (Crustacea), arrives in Ireland. Aquatic Invasions. 3 (2), 257-259. http://www.aquaticinvasions.ru/2008/AI_2008_3_2_Minchin_Holmes.pdf DOI:10.3391/ai.2008.3.2.19

Mordukhai-Boltovskoi F D, 1939. [English title not available]. (O reliktovoi faune nizovev Dona.). Trudy Rostovksogo Oblastnogo Biologicheskogo Obshchestva. 69-76.

Pienimäki M, Leppäkoski E, 2004. Invasion pressures on the Finnish Lake District: invasion corridors and barriers. Biological Invasions. 331-346.

Pothoven S A, Grigorovich I A, Fahnenstiel G L, Balcer M D, 2007. Introduction of the Ponto-Caspian bloody-red mysid Hemimysis anomala into the Lake Michigan basin. Journal of Great Lakes Research. 285-292.

Rehage H O, Terlutter H, 2002. Hemimysis anomala Sars (Crustacea, Mysidacea) in the Mittellandkanal near Recke-Obersteinbeck (Nordrhein-Westfalen). (Hemimysis anomala Sars (Crustacea, Mysidacea) im Mittellandkanal bei Recke-Obersteinbeck (Nordrhein-Westfalen).). Lauterbornia. 47-48.

Salemaa H, Hietalahti V, 1993. Hemimysis anomala G. Sars 1907 (Crustacea: Mysidacea) - immigration of a Ponto-Caspian mysid into the Baltic Sea. Annales Zoologici Fennici. 271-276.

Schleuter A, Schleuter M, 1998. Dendrocoelum romanodanubiale (Turbellaria, Tricladia) and Hemimysis anomala (Crustacea: Mysidacea), two new neozoans in the River Main. (Dendrocoelum romanodanubiale (Turbellaria, Tricladia) und Hemimysis anomala (Crustacea: Mysidacea) zwei weitere Neozoen im Main.). Lauterbornia. 125-127.

Stubbington R, Terrell-Nield C, Harding P, 2008. The first occurrence of the Ponto-Caspian invader, Hemimysis anomala G. Sars, 1907 (Mysidacea) in the U.K. Crustaceana. 81 (1), 43-55.

Verslycke T, Janssen C, Lock K, Mees J, 2000. First occurrence of the Pontocaspian invader Hemimysis anomala (Sars, 1907) in Belgium (Crustacea: Mysidacea). Belgian Journal of Zoology. 130 (2), 157-158.

Wittmann K J, 2007. Continued massive invasion of Mysidae in the Rhine and Danube river systems, with first records of the Mysidacea (Crustacea: Malacostraca: Pericarida) for Switzerland. Revue Suisse de Zoologie. 65-86.

Wittmann K J, Ariani A P, 2009. Reappraisal and range extension of non-indigenous Mysidae (Crustacea, Mysida) in continental and coastal waters of eastern France. Biological Invasions. 11 (2), 401-407. http://www.springerlink.com/content/kx20151n83677237/?p=d48c11cd995e4d45b8e6c4892ae212b9&pi=22 DOI:10.1007/s10530-008-9257-7

Wittmann K J, Theiss J, Banning M, 1999. The planktonic drift of Mysidacea and Decapoda and its significance with regard to the spread of neozoa in the Main-Donau river system. (Die drift von Mysidaceen und Dekapoden und ihre Bedeutung für die Ausbrietung von Neozoen im Main-Donau-System.). Lauterbornia. 53-66.

Zhuravel P A, 1959. On the biology and ecology of mysids experimentally introduced into water reservoirs and other bodies of water in the Ukraine in order to enrich the feeds provision of fishes. Zoologicheskij Zhurnal. 987-990.

Links to Websites

Organizations

Europe: DAISIE - Delivering Alien Invasive Species Inventories for Europe, Web-based service, http://www.europe-aliens.org

Northern Ireland: QUERCUS - Biodiversity and Conservation Biology Centre, School of Biological Sciences, Queen's University,, Belfast, http://www.qub.ac.uk/sites/Quercus/

USA: NCRAIS - National Centre for Research on Aquatic Invasive Species, NOAA/GLERL 2205 Commonwealth Boulevard, Ann Arbor, Michigan, 48105, http://www.glerl.noaa.gov/

Contributors

29/04/09 Original text by:

Rachel Stubbington, Loughborough University, Department of Geography, UK

Distribution Maps