identifier	taxonID	type	CVterm	format	language	title	description	additionalInformationURL	UsageTerms	rights	Owner	contributor	creator	bibliographicCitation
03E97B2DFFF85860607AFE8FFB68CAD7.text	03E97B2DFFF85860607AFE8FFB68CAD7.taxon	http://purl.org/dc/dcmitype/Text	http://rs.tdwg.org/ontology/voc/SPMInfoItems#GeneralDescription	text/html	en	Grandidierella bonnieroides Stephensen 1947	<html xmlns:mods="http://www.loc.gov/mods/v3">
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            <p> Grandidierella bonnieroides Stephensen, 1947</p>
            <p> Grandidierella bonnieroides is a cosmopolitan circumtropical species distributed in tropical and temperate regions (Myers 1970, 2009; LeCroy et al., 2009). This aorid is very abundant in the Caribbean and on the tropical west Atlantic coast and to date is recorded in Arabian Gulf, India, South Africa, Indonesia, Mexico, Puerto Rico, Colombia, Cuba, Bahamas, Brazil, and North America (Myers, 1970; Zimmerman et al., 1979; Stoner, 1980; Heard, 1982; Lalana‐Rueda and Gosselck, 1986; Virnstein and Curran 1986; Stearns and Dardeau 1990; Stoner and Acevedo 1990; Ortiz and Lalana, 1996, 2010; Ortiz and Lemaitre 1997; LeCroy et al., 2002; Satheeshkumar, 2011; Paz-Rios and Ardisson, 2013; Hindarti et al., 2015; Sweatman et al., 2017; Manokaran et al., 2021; Winfield et al., 2023). This species was originally described in the Netherlands Antilles, Caribbean Sea (Stephensen, 1933). Regarding the Mediterranean basin, it has recently been reported in Israel as a non-indigenous species (Lo Brutto et al., 2016). How this aorid arrived in Mediterranean water has not yet been determined but the most likely transport vectors could be ballast water and ship fouling (Lo Brutto et al., 2016). </p>
            <p> In its natural areas of distribution,  G. bonnieroides is considered a dominant species in estuarine and euryhaline environments (Stearns and Dardeau, 1990). In addition, this aorid has also been established in intertidal mangroves (Satheeshkumar, 2011), seagrass meadows such as Stryngodium filiforme,  Halodule wrightii and  Thalassia testudinum (Stoner et al., 1980; Virnstein and Curran, 1986; Sweatman et al., 2017), soft bottoms in shallow bays, tide pools (Heard, 1982) and muddy bottoms with sparse vegetation (Oliva-Rivera, 1998).  Grandidierella bonnieroides can also exploit muddy substrates characterized by low oxygen tension (Day, 1981). </p>
            <p> This species is considered a gregarious “detritus- blanket tube-builder” as it lives inside masses of detritus that are utilised for enrolling themselves in a blanket-like semi-permanent tube (Thomas, 1976; Barnard et al., 1991). The tube is agglutinating with silk and sediments particles, micro and macroalgae debris and foraminifera (Barnard et al., 1991; Ortiz and Lalana, 2010).  Grandidierella bonnieroides is a subsurface interstitial omnivore deposit feeder (Manokaran et al., 2021) and is classified as a microphage that feeds mainly on epiphytic diatoms and debris accumulated on vegetation (Zimmerman et al., 1979). Moreover, this species can change its feeding modes encompassing filterfeeders, grazer, detritivore, and deposit feeders according to food availability (Thomas, 1976; LeCroy et al., 2002; Reis Filho et al., 2018) and promotes nutrient recycling by reintegrating carbon into trophic networks (Reis Filho et al., 2018). </p>
            <p> Grandidierella bonnieroides is cryptic in colour and behaviour and hides in sediments to reduce its vulnerability to visual predators (Stoner, 1980). In fact, in estuarine environments, this species is an important food resource for benthic and nektonic species, especially fish, crabs and penaeid shrimps (Lalana‐Rueda and Gosselck, 1986; Paiva and Da Silva, 1998). </p>
            <p> This species is regarded as an opportunistic pollution indicator (Grizzle, 1984; Barnard et al., 1991) and has been employed in ecotoxicological studies to assess sediment toxicity and the presence of chemical compounds in environments (Hindarti et al., 2015; Reis Filho et al., 2018). Furthermore,  G. bonnieroides is also known to colonize substrates that undergo recurrent defaunation, sometimes forming dense populations (Santos and Simon, 1980). </p>
            <p> The resistance characteristics of this species may have contributed to its successful colonization of Haifa Bay (Israel), which is characterized by anthropogenic pollution and eutrophication (Herut &amp; IOLR Scientists, 2022; Lo Brutto et al., 2016). Our analyses revealed the presence of 243 individuals of  G. bonnieroides distributed over soft bottoms located at depths between 7.8 and 11.7 m. The species was found with high abundance close to the Haifa harbour, in the only site characterized by the presence of coarse sediment (HM2.1 station, in 2014, 227 individuals); subsequently, a few individuals were found in a site within Haifa Bay, characterized by finer sediments (HM27 station, in 2015, 7 individuals). A single individual was sampled along the Israeli coast in 2016 (H19 station), and, finally, the species was again recorded in 2017 at its first settlement site (HM2.1 station, 8 individuals). </p>
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	https://treatment.plazi.org/id/03E97B2DFFF85860607AFE8FFB68CAD7	Public Domain	No known copyright restrictions apply. See Agosti, D., Egloff, W., 2009. Taxonomic information exchange and copyright: the Plazi approach. BMC Research Notes 2009, 2:53 for further explanation.		Plazi	Iaciofano, Davide;Mancini, Emanuele;Lubinevsky, Hadas;Brutto, Sabrina Lo	Iaciofano, Davide, Mancini, Emanuele, Lubinevsky, Hadas, Brutto, Sabrina Lo (2024): The amphipod fauna assemblage along the Mediterranean Israeli coast, a spatiotemporal overview. Ecologica Montenegrina 80: 244-272, DOI: 10.37828/em.2024.80.22, URL: https://doi.org/10.37828/em.2024.80.22
03E97B2DFFF7586F638EFF20FE2CCB8C.text	03E97B2DFFF7586F638EFF20FE2CCB8C.taxon	http://purl.org/dc/dcmitype/Text	http://rs.tdwg.org/ontology/voc/SPMInfoItems#GeneralDescription	text/html	en	Bathyporeia guilliamsoniana (Spence Bate 1857)	<html xmlns:mods="http://www.loc.gov/mods/v3">
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            <p> Bathyporeia guilliamsoniana (Spence Bate, 1857)</p>
            <p>This species is present in the northeastern Atlantic, North Sea, Marmara Sea and Black Sea. It is recorded in the Mediterranean and European waters: France, Scotland, England, Italy, Egypt, Israel Spain, Belgium, Netherlands, Algeria, Norway, Portugal, Tunisia and Turkey (Sars, 1890 -95; Gottlieb, 1960; Atta, 1988; N'Da, 1992; Eleftheriou and Robertson, 1992; Marques and Bellan-Santini, 1993; Bakalem, 1998; d'Udekem d'Acoz and Vader, 2005; Kirkim et al., 2006; Colosio et al., 2007; Pérez‐Domingo et al., 2008; Kröncke, 2011; Passarelli et al., 2012; Curatolo et al., 2013; Navarro-Barranco et al., 2013; Bakir and Katağan, 2014; Mülayim et al., 2015a,b; Coates et al., 2016; Belatoui et al., 2017; Mayer et al., 2018; Wijnhoven et al., 2018; Ballesteros et al., 2020).</p>
            <p> All the species of the genus  Bathyporeia are considered burrowers and confined to sandy bottoms (Toulmond, 1964); in fact,  B. guilliamsoniana is generally associated with shallow water well sorted fine sand sensu Pérès &amp; Picard (1964) and other sand sublittoral biocenosis (Jones, 1950; Diaviacco and Bianchi, 1987; Occhipinti Ambrogi et al., 1988; Robertson et al., 1989; Eleftheriou and Robertson, 1992; Heip and Craeymeersch, 1995; de-la-Ossa-Carretero et al., 2010) and often dominates in the communities of the shallow-water sand habitat (Elmhirst, 1932). In detail,  B. guilliamsoniana has been found on several types of soft substrates such as fine depositional sands with  Tellina spp. (Warwick and Davies, 1977),  Spisula subtruncata sands, sand with shells fragments, intertidal sand (Robertson et al., 1989; De Grave and Casey, 2000; Pérez‐Domingo et al., 2008), lagoon sands (Reid, 1941; Diaviacco and Bianchi, 1987), muddy sands and mud (Kirkim et al., 2006). The optimal sediment type for this bathyporeid is sand with median grain size with high percentage of carbonate particles but this species can live on slightly coarser sediments (Toulmond, 1964; Degraer et al., 2006). Moreover,  B. guilliamsoniana can be observed rarely on  Mytilus galloprovincialis facies and oyster beds, in photophilic algae communities (Millar, 1961; Mülayim et al., 2015a,b) and in areas subject to anthropogenic impact (Bakalem, 1998; Colosio et al., 2007). </p>
            <p>Regarding its bathymetric distribution range this species is generally observed in shallow waters between 0.5 and 20 m (Bossanyi, 1957; Occhipinti-Ambrogi et al., 1988; Kirkim et al., 2006; de-la-Ossa-Carretero et al., 2010; Curatolo et al., 2013; Mülayim et al., 2015a,b; Belatoui et al., 2017) but some specimens have also been sampled at about 75 m depth (d’Udekem d’Acoz, 2004).</p>
            <p> Bathyporeia guilliamsoniana feeds on detritus (Navarro-Barranco et al., 2013) and eats organic particles adhered to sand grains (Nicolaisen and Kanneworff, 1969), for these reasons can be considered as selective deposit-feeders (Wolff, 1973). This species actively burrows into the sand by the action of the head, used to penetrate the sediment, and use the anterior appendages for generate an intense “ventral groove” current (Watkin, 1939a, b). This amphipod species shows a pronounced sexual dimorphism (d'Udekem d’Acoz, 2004) and is capable of nocturnal vertical movement (d'Udekem d’Acoz and Vader, 2005); particularly, the adult males swim in the water column at night and these vertical displacements are probably regulated by lunar and tidal cycles (Watkin, 1939b; d'Udekem d’Acoz, 2004; d'Udekem d’Acoz and Vader, 2005). Some authors have pointed out the presence of parasites on the body of  B. guilliamsoniana ; this species can be infested both by epizoan ciliates (Wijnhoven et al., 2018) and copepods such as  Sphaeronella paradoxa Hansen, 1897 (d'Udekem d’Acoz, 2004). </p>
            <p> A total of 1383 individuals of  B. guilliamsoniana exclusively on soft substrate localized between 7.8 and 12.82m depth was collected. The species  Bathyporeia guilliamsoniana was observed to have high abundances in the central section of the Israeli coastline (H3-H41 stations) and lower abundances in the southernmost areas. In contrast, Haifa Bay exhibited the occasional presence of a few individuals supporting that the species was consistently absent in the stations characterized by high levels of anthropogenic activities. </p>
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	https://treatment.plazi.org/id/03E97B2DFFF7586F638EFF20FE2CCB8C	Public Domain	No known copyright restrictions apply. See Agosti, D., Egloff, W., 2009. Taxonomic information exchange and copyright: the Plazi approach. BMC Research Notes 2009, 2:53 for further explanation.		Plazi	Iaciofano, Davide;Mancini, Emanuele;Lubinevsky, Hadas;Brutto, Sabrina Lo	Iaciofano, Davide, Mancini, Emanuele, Lubinevsky, Hadas, Brutto, Sabrina Lo (2024): The amphipod fauna assemblage along the Mediterranean Israeli coast, a spatiotemporal overview. Ecologica Montenegrina 80: 244-272, DOI: 10.37828/em.2024.80.22, URL: https://doi.org/10.37828/em.2024.80.22
03E97B2DFFF7586E604DF8D3FEA7CF11.text	03E97B2DFFF7586E604DF8D3FEA7CF11.taxon	http://purl.org/dc/dcmitype/Text	http://rs.tdwg.org/ontology/voc/SPMInfoItems#GeneralDescription	text/html	en	Cheiriphotis mediterranea Myers 1983	<html xmlns:mods="http://www.loc.gov/mods/v3">
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            <p> Cheiriphotis mediterranea Myers, 1983</p>
            <p>This corophiid is endemic to the Levantine basin; it had been reported only in Israel, but recent observations in Turkey extended the northernmost area of distribution (Myers 1983; Sorbe et al. 2002; Bakir and Katağan, 2014; Çinar et al., 2015; Lo Brutto and Iaciofano, 2020; Lo Brutto et al., 2022). It is important to point out that though its collection has been limited to the eastern Mediterranean coast, some individuals were also observed in semi-enclosed bays in China (Ren, 2006; Shi et al., 2022), a geographical occurrence that needs to be confirmed. Since its limited range, this amphipod is considered a relict species that survived the paleogeographic and paleoclimatic events that affected the Mediterranean Sea (Lo Brutto et al., 2022).</p>
            <p> Cheiriphotis mediterranea is an infralittoral filter-feeder species and was generally observed on fine sand, coarse sand, detritic rubble and sandy-muddy bottoms also in association with the photid  Photis longicaudata (Sorbe et al., 2002; Bakir and Katağan, 2014; Lo Brutto et al., 2022). Its bathymetric distribution ranges between 3 and 38 m depth, with maximum abundances recorded between 10 and 25 m (Lo Brutto et al., 2022). </p>
            <p> High abundances of this species have been observed in the anthropised Haifa Bay and, for this reason,  C. mediterranea seems to be a good bioindicator of environmental contamination such as pollutants, organic matter, and high carbon levels. The presence of 2619 specimens of  C. mediterranea , with a significant peak (1805 individuals) in 2014 in Haifa Bay, was distributed at depths between 7.8 and 12.81 m. </p>
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	https://treatment.plazi.org/id/03E97B2DFFF7586E604DF8D3FEA7CF11	Public Domain	No known copyright restrictions apply. See Agosti, D., Egloff, W., 2009. Taxonomic information exchange and copyright: the Plazi approach. BMC Research Notes 2009, 2:53 for further explanation.		Plazi	Iaciofano, Davide;Mancini, Emanuele;Lubinevsky, Hadas;Brutto, Sabrina Lo	Iaciofano, Davide, Mancini, Emanuele, Lubinevsky, Hadas, Brutto, Sabrina Lo (2024): The amphipod fauna assemblage along the Mediterranean Israeli coast, a spatiotemporal overview. Ecologica Montenegrina 80: 244-272, DOI: 10.37828/em.2024.80.22, URL: https://doi.org/10.37828/em.2024.80.22
03E97B2DFFF6586E6055FD5EFC12CA35.text	03E97B2DFFF6586E6055FD5EFC12CA35.taxon	http://purl.org/dc/dcmitype/Text	http://rs.tdwg.org/ontology/voc/SPMInfoItems#GeneralDescription	text/html	en	Megaluropus massiliensis Ledoyer 1976	<html xmlns:mods="http://www.loc.gov/mods/v3">
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            <p> Megaluropus massiliensis Ledoyer, 1976</p>
            <p> Megaluropus massiliensis is an endemic Mediterranean species that has also colonized the Black Sea (Sorbe et al., 2002; Karaçuha et al., 2009; Mülayim, 2021; Grinstov, 2022). It has been recorded in Algeria, Corsica, France, Italy, Israel, Greece, Morocco, Spain, Tunisia and Turkey (León and Corrales, 1995; Conradi &amp; López-González, 1999; Sánchez-Jerez et al., 1999; San Vincente and Sorbe, 1999; Sorbe et al., 2002; Scipione et al., 2005; Kirkim et al., 2006; Sezgi̇n and Katağan, 2007; Luís, 2007; Karaçuha et al., 2009; Vázquez-Luis et al., 2009; de-la-Ossa-Carretero et al., 2010, 2012; Lorenti et al., 2011; Bakir, 2012; Lattanzi et al., 2013; Bakir &amp; Katağan, 2014; Guerra- García et al., 2014; Çinar et al., 2015; Mülayim et al., 2015a,b; Maidanou et al., 2017, 2021; Zakhama-Sraieb et al., 2017; Targusi et al., 2019; Navarro-Barranco et al., 2020; Bakalem et al., 2024; Saenz-Arias et al., 2024). </p>
            <p> This amphipod is a fossorial filter feeder species (de-la-Ossa-Carretero et al., 2012), and it is also an important component of the hyperbenthic fauna of surface sandy substrates (León &amp; Corrales, 1995; Galparsolo, 1999). Indeed,  M. massiliensis commonly colonizes fine sand, very fine sand, muddy sand and, less commonly, mud (Conradi and López-González, 1999; de-La-Ossa-Carretero et al., 2010; Targusi et al., 2019; Mülayim, 2021). In some studies, this species has been observed in association with  Spisula subtruncata sand (Mülayim et al., 2015a) and  Phaseolina sludge zoocenosis (Sezgi̇n and Katağan, 2007).  Megaluropus massiliensis has also been observed in relation to shallow-water phanerogam meadows, such as  Posidonia oceanica ,  Cymodocea nodosa ,  Zostera marina and  Zostera noltii (Sánchez-Jerez et al, 1999; San Vincente and Sorbe, 1999; Karaçuha et al., 2009; Vázquez-Luis et al., 2009) and with rocky substrates colonized by photophilic macroalgae (Navarro-Barranco et al., 2020). Some studies have shown that this species also inhabits areas characterized by the presence of the caulerpaces  Caulerpa racemosa and  C. prolifera (Luís, 2007; Vázquez-Luis et al., 2009; Lorenti et al., 2011; Maidanou et al., 2017, 2021). </p>
            <p>This megaluropid is most abundant in shallow coastal waters between 1 and 10 m (León &amp; Corrales, 1995; Mülayim et al., 2015a; Maidanou et al., 2017; Saenz-Arias et al., 2024) but some authors have reported it at greater depths up to about 50 m (Scipione et al., 2005; Conradi and López-González, 1999; Lattanzi et al., 2013).</p>
            <p> Ecologically,  M. massiliensis was considered particularly sensitive to pollution and organic enrichment (de-la-Ossa-Carretero et al., 2012; Çinar et al., 2015). However, Lattanzi et al. (2013) observed that this amphipod is tolerant to the increase of fine sediment in suspension/deposition.  Megaluropus massiliensis feeds on suspended detritus and planktonic crustaceans (Guerra-García et al., 2014); it is most active at night and can be sampled using light traps (Saenz-Arias et al., 2024), indicating that it probably moves vertically along the water column. </p>
            <p> Our analyses revealed the presence of 468 individuals exclusively on soft sandy bottoms, distributed at depths between 7.8 and 12.81 m.  Megaluropus massiliensis was found particularly numerous within Haifa Bay. This species demonstrated low abundances along the entire southern coast of Israel, with two notable peaks in abundance at sites H13 and H28. </p>
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	https://treatment.plazi.org/id/03E97B2DFFF6586E6055FD5EFC12CA35	Public Domain	No known copyright restrictions apply. See Agosti, D., Egloff, W., 2009. Taxonomic information exchange and copyright: the Plazi approach. BMC Research Notes 2009, 2:53 for further explanation.		Plazi	Iaciofano, Davide;Mancini, Emanuele;Lubinevsky, Hadas;Brutto, Sabrina Lo	Iaciofano, Davide, Mancini, Emanuele, Lubinevsky, Hadas, Brutto, Sabrina Lo (2024): The amphipod fauna assemblage along the Mediterranean Israeli coast, a spatiotemporal overview. Ecologica Montenegrina 80: 244-272, DOI: 10.37828/em.2024.80.22, URL: https://doi.org/10.37828/em.2024.80.22
03E97B2DFFF5586D63C5FF20FE6ACA9A.text	03E97B2DFFF5586D63C5FF20FE6ACA9A.taxon	http://purl.org/dc/dcmitype/Text	http://rs.tdwg.org/ontology/voc/SPMInfoItems#GeneralDescription	text/html	en	Perioculodes longimanus (Spence Bate & Westwood 1868)	<html xmlns:mods="http://www.loc.gov/mods/v3">
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            <p> Perioculodes longimanus (Spence Bate &amp; Westwood, 1868)</p>
            <p>This species is widely distributed in the Mediterranean Basin, Black Sea and European waters and is reported in France, Scotland, England, Spain, Italy, Anatolia, Germany, Norway, Algeria, Ireland, Portugal, Spain, Cyprus, Sweden, Turkey, Romania, Greece, Holland, Tunisia, and Israel (Falciai and Spadini, 1985; Buhl-Jensen, 1986; Occhipinti-Ambrogi et al., 1988; Dauvin and Gentil, 1990; Buhl-Jensen and Fosså, 1991; Faasse and Stikvoort, 2002; Blanchet et al., 2005; Kirkim et al., 2006; Sezgin and Katağan, 2007; Nickell et al., 2009; Zakhama-Sraieb et al., 2009, 2017; de-la-Ossa-Carretero et al. 2010; Sezgin et al., 2010; Schückel et al., 2011; Carvalho et al., 2012; Navarro-Barranco et al., 2013; Nikitik and Robinson, 2003; Kudrenko et al., 2016; Misic et al., 2016; Belatoui et al., 2017; Maidanou et al., 2017; Ballesteros et al., 2020; Rousou et al., 2020; Mülayim, 2021; Tănase et al., 2022).</p>
            <p> Perioculodes longimanus is exclusively associated with soft infralittoral substrates and sand sublittoral biocenosis (Buhl-Jensen and Fosså, 1991, Sezgin and Katağan, 2007; Ballesteros et al., 2020) although it has also been found on deep substrates and bathyal bottom (Cartes et al, 2007). Due to the close association between this species and sandy substrates,  P. longimanus is considered an exclusive species of the well calibrate fine sands biocenosis sensu Pérès &amp; Picard (1964) (Falciai and Spadini, 1985; Niccolai et al., 1993). The bottom types and sands communities in which this species is observed are intertidal sands (Viéitez and Baz, 1988; Robertson et al., 1989), fine sands (Lourido et al., 2010), coarser sands (Parker, 1984), mud, muddy sands and clay (Kirkim et al., 2006), slightly gravelly sandy mud (Cruz et al., 2003), sand and mud biodetrital bottom (Dumitrache et al., 2013), very fine sands with  Abra alba -  Tellina fabula communities (Warwick and Davies, 1977; Dauvin and Gentil, 1990),  Venus striatula sand communities (Klein et al., 1975). Furthermore, this oedicerotid is also present in substrates colonized by marine phanerogams and algae such as  Posidonia oceanica ,  Cymodocea nodosa ,  Zostera marina ,  Z. noltii and  Caulerpa prolifera (Sánchez-Jerez et al., 1999; Karaçuha al., 2009; Bakir and Katağan, 2014; Bellisario et al., 2016; Maidanou et al., 2017), and is observed also in association with the communities of shallow hydrothermal vents (Dando et al., 1995). </p>
            <p> Perioculodes longimanus can be considered resistant to pollution (Belatoui et al., 2017) and in fact it was reported in estuarine areas and in other localities characterised by the presence of anthropogenic discharges such as fish farms discharges, oil spill and waste pollution (Bakalem, 1998; Pearson and Black, 2000; Faasse and Stikvoort, 2002; Nickell et al., 2009; Sánchez-Moyano and García-Asencio, 2010; Dumitrache et al., 2013; Nikitik and Robinson, 2003; de-la Ossa-Carretero et al., 2016); but in this context, it is important to emphasize that de-la-Ossa-Carretero et al. (2012) have pointed out that this species showed high sensitivity to sewage pollution. </p>
            <p> This species is considered eurybathic and associated with hyperbenthic communities (Greze, 1968; Cartes et al., 2009; Koulouri et al., 2013; Navarro-Baranco et al., 2013; Guerra-García et al., 2013). Also, even if  P. longimanus is common and abundant in shallow waters between 1 and 30 m (Klein et al., 1975; Dauvin and Gentil, 1990; Buhl-Jensen &amp; Fosså, 1991; Dumitrache et al., 2013; Ballesteros et al., 2020), its bathymetric distribution can be deeper up to about 100 m (Viéitez and Baz, 1988; Cartes et al., 2009; Koulouri et al., 2013). Probably the high variability of its bathyal distribution range is related to its regular vertical migrations in the water column; in fact,  P. longimanus performs vertical nocturnal migrations of variable amplitude (Watkin, 1939b; Sorbe, 1982) and, in some areas, the abundance of this species varies on a daily scale resulting in an increase in its abundance during the night hours (Bossanyi, 1957). </p>
            <p> Although this oedicerotid is not characterised by sexual dimorphism generally the female individuals are larger in size. Beare and Moore (1998) analyzed its sex ratio and observed that there is a dominance of females in coastal water populations. In addition, these authors pointed out that female specimens can be parasitized by the copepod  Sphaeronella minuta Scott T., 1904 . </p>
            <p> Perioculodes longimanus is considered a common prey of some flatfish such as  Buglossidium luteum (Risso, 1810) ,  Arnoglossus laterna (Walbaum, 1792) ,  Limanda limanda (Linnaeus, 1758) and  Pleuronectes platessa Linnaeus, 1758 (Beare and Moore, 1997; Schückel et al., 2011). </p>
            <p> In this work, 3127 specimens of  P. longimanus were observed on soft substratum distributed over a bathymetric range of 7.8 - 12.81 m.  Perioculodes longimanus exhibited a uniform distribution along the entire coastline, except for the anthropised site of Haifa port (HM27), where the abundance was relatively low. </p>
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	https://treatment.plazi.org/id/03E97B2DFFF5586D63C5FF20FE6ACA9A	Public Domain	No known copyright restrictions apply. See Agosti, D., Egloff, W., 2009. Taxonomic information exchange and copyright: the Plazi approach. BMC Research Notes 2009, 2:53 for further explanation.		Plazi	Iaciofano, Davide;Mancini, Emanuele;Lubinevsky, Hadas;Brutto, Sabrina Lo	Iaciofano, Davide, Mancini, Emanuele, Lubinevsky, Hadas, Brutto, Sabrina Lo (2024): The amphipod fauna assemblage along the Mediterranean Israeli coast, a spatiotemporal overview. Ecologica Montenegrina 80: 244-272, DOI: 10.37828/em.2024.80.22, URL: https://doi.org/10.37828/em.2024.80.22
03E97B2DFFF4586C63AAFF20FB45C992.text	03E97B2DFFF4586C63AAFF20FB45C992.taxon	http://purl.org/dc/dcmitype/Text	http://rs.tdwg.org/ontology/voc/SPMInfoItems#GeneralDescription	text/html	en	Photis longicaudata (Spence Bate & Westwood 1862)	<html xmlns:mods="http://www.loc.gov/mods/v3">
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            <p> Photis longicaudata (Spence Bate &amp; Westwood, 1862)</p>
            <p> Photis longicaudata is considered Atlantic-Indo-Mediterranean species and its distribution extends to the Indian Ocean, Barents Sea, South Africa, India, China, Korean Peninsula, Caribbean Sea, Costa Rica, Venezuela, Gulf of Mexico, Indonesia, Philippine, and New Zealand (Bellan-Santini, 1990). In the Mediterranean Basin and European waters this species is recorded in France, Ireland, Scotland, Spain, Israel, Italy, Portugal, England and Algeria (Falconetti, 1970; Bellan-Santini and Ledoyer, 1973; Parker, 1984; Falciai and Spadini, 1985; Dauvin, 1987; Dauvin, 1999; Moore and Cameron, 1999; Sorbe et al., 2002; Miloslavich et al., 2010; de-la-Ossa-Carretero et al., 2012; Lo Brutto et al., 2016; Plicanti et al., 2017; Navarro-Barranco et al., 2017). </p>
            <p> This photid can be observed on several types of substrates such as fine sands (Dauvin, 1987), muddy sands and mud (Falciai and Spadini, 1985), detritic substrates and coralline algae, hard and artificial substrates (Flynn and Valèrio-Berardo, 2009, 2012; de-la-Ossa-Carretero et al., 2012) and  Sabellaria alveolata biocostructions (Plicanti et al., 2017).  Photis longicaudata is also abundant in the photophilic and intertidal algae epifaunal community and is founded in association with some species of  Sargassum (e.g.  Sargassum stenophyllum ) (Tanaka and Leite, 2003; Ortiz et al., 2005). Moore and Cameron (1999) observed some specimens of  P. longicaudata among the tentacles of the anthozoan  Cerianthus lloydii Gosse, 1859 and hypothesized that this amphipod exploits this cnidarian to gain protection and defence from predators. Moreover,  P. longicaudata is also considered resistant to pollution and has been found in areas affected by anthropogenic impact and sewage pollution (Flynn and Valèrio-Berardo, 2009, 2012; de-la-Ossa-Carretero et al., 2012). </p>
            <p>This species is most abundant between 0 and 50 m but it can also exploit deep substrates located at depths of about 200 m (Ortiz et al., 2005).</p>
            <p> Photis longicaudata is considered a tube dweller opportunistic suspension feeder as it builds small muddy tubes that can form dense aggregations in fouling communities (Moore and Cameron, 1999; Flynn and Valério-Berardo, 2009). </p>
            <p> Our analyses revealed the presence of 988 individuals of this species which was distributed at depths between 7.8 and 11.7 m.  Photis longicaudata was recorded mainly at the site HM2.1 where an increase in abundance was exhibited in 2014 (751 individuals). A single observation was recorded in 2011 at the Haifa Port site (HM27 station; 118 individuals), while the species was present with occasional occurrences along the southernmost portion of the Israel coasts (H19-H28). </p>
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	https://treatment.plazi.org/id/03E97B2DFFF4586C63AAFF20FB45C992	Public Domain	No known copyright restrictions apply. See Agosti, D., Egloff, W., 2009. Taxonomic information exchange and copyright: the Plazi approach. BMC Research Notes 2009, 2:53 for further explanation.		Plazi	Iaciofano, Davide;Mancini, Emanuele;Lubinevsky, Hadas;Brutto, Sabrina Lo	Iaciofano, Davide, Mancini, Emanuele, Lubinevsky, Hadas, Brutto, Sabrina Lo (2024): The amphipod fauna assemblage along the Mediterranean Israeli coast, a spatiotemporal overview. Ecologica Montenegrina 80: 244-272, DOI: 10.37828/em.2024.80.22, URL: https://doi.org/10.37828/em.2024.80.22
03E97B2DFFF4587B6030FAD9FC73CE1F.text	03E97B2DFFF4587B6030FAD9FC73CE1F.taxon	http://purl.org/dc/dcmitype/Text	http://rs.tdwg.org/ontology/voc/SPMInfoItems#GeneralDescription	text/html	en	Urothoe grimaldii Chevreux 1895	<html xmlns:mods="http://www.loc.gov/mods/v3">
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            <p> Urothoe grimaldii Chevreux, 1895</p>
            <p>This urotoid is reported in Atlantic Ocean, Indian Ocean, and Mediterranean Sea (Sorbe et al., 2002) and in particular for the European waters and Mediterranean Basin is observed in France, England, Germany, Spain, Portugal, Italy, Israel, Tunisia and Turkey (Gottlieb, 1960; Toulmond, 1964; Ladle, 1975: Kingston and Rachor, 1982; Grémare et al., 1998; Martínez and Adarraga, 2001; Sorbe et al., 2002; Marín-Guirao et al., 2005; Covazzi Harriague et al., 2008; Moreira et al., 2008; Bakalem et al., 2009; Zakhama-Sraieb et al., 2009; Bakir and Katağan, 2014; Sampaio et al., 2016).</p>
            <p> Urothoe grimaldii is considered a characteristic species of the well sorted fine sand sensu Pérès &amp; Picard (1964) (Dauvin et al., 2017) and is closely associated with surface and intertidal soft substrates (Grémare et al.,1998; Momtazi and Maghsoudlou, 2022). This species has been reported on different types of seabeds and intertidal zone of sandy beach (Dahl, 1952; Daief et al., 2014), sandflats (Wynberg and Branch, 1997; Siebert and Branch, 2007), coarse sands (Penas and Gonzalez, 1983; Moreira et al., 2008) fine sands (Bakalem et al., 2009),  Tellina fabula sand communities (Kingston and Rachor, 1982),  Spisula subtruncata sand community (Grémare et al.,1998),  Ampelisca brevicornis fine sand community (Toulmond, 1964),  Amphioxus sands (Chen et al., 2013), mud, mud and sand mixture (Bakir and Katağan, 2014). Moreover, it was observed in lagoon environments (Wynberg and Branch, 1997; du Plessis and Pillay, 2022), in soft substrates vegetates by  Fucus spp. and  Caulerpa cylindracea (Toulmond, 1964; Lorenti et al., 2011) and as epibiont of loggerhead sea turtle  Caretta caretta (Zakhama-Sraieb et al., 2009) .  Urothoe grimaldii is also adapted to live in polluted coastal areas (Ibanez et al., 1993) and can survive near urban discharges (Avramidi et al., 2022). </p>
            <p>This species lives exclusively in shallow coastal waters between 0.5 and 20 m (Penas and Gonzalez, 1983; Moreira et al., 2008; Bakir and Katağan, 2014) and performs seasonal depth migrations. Indeed, it descends to greater depths in summer until it reaches a maximum depth of around 20-30 m (Amouroux, 1974).</p>
            <p> Like all species of the genus  Urothoe ,  U. grimaldii is considered a predator carnivorous species that preys on benthic meiofauna (Macdonald et al., 2010). Females of this species generally live for two years, while the less long-lived males mature within a year (Ladle, 1975). This urothoid can also exploit the burrows of some benthic fossorial species as a source of protection and prey seeking, in fact Goulliart (1952) observed that  U. grimaldii can live in the tunnels burrowed by the polychaete  Arenicola marina (Linnaeus, 1758) . This amphipod is preyed by coastal fish species such as gobies (Villiers, 1982) and is part of the diet of the flamingo  Phoenicopterus roseus Pallas, 1811 (du Plessis and Pillay, 2022). </p>
            <p> In this work, 1593 individuals of this species were sampled and identified.  Urothoe grimaldii was observed only on mobile substrates distributed between 8.41 and 12.81 m.  Urothoe grimaldii has been consistently observed along the entire coast of Israel, with occasional records in Haifa Bay, but never in the anthropised sites (HM2.1 and HM27). </p>
            <p>Spatiotemporal variation</p>
            <p> The temporal variation in the richness of all the taxa, i.e. species and genus taxa, and their total abundance was shown for each station during the consecutive years (Figure 4). In general, the highest abundances were not linked to the highest richness, probably due to the low number of species and the features of sandy amphipod assemblages where local explosions of a few species often occur. An example is the occurrence of 1805  Cheiriphotis mediterranea individuals in station HM2.1 in the year 2014, not comparable to a proportional increase in species richness (Figure 4). </p>
            <p>The absence of correlation between the abundance and the species richness was caused by a differential contribution of different species. The fluctuations in abundance were due to an increase in the dominant species not the rare and sporadic species; in contrast, the richness was determined by the total number of species and taxa, and influenced by the occasional taxa (Figure 4).</p>
            <p>..continued on the next page</p>
            <p> The nMDS did not reveal any temporal variation which could have been associated with changes over the eight years (Figure 5). The contribution of the most abundant species to the taxocenosis profile (SIMPER analysis in Supplement) supported such result, as  Perioculodes longimanus and  Urothoe grimaldii were the species with the maximum weight in similarity analyses, showing a stable presence. To explore the spatial variability, the long-term monitoring supported the division into two principal zones. The nMDS analysis (Figure 5) showed a discrepancy in amphipod assemblage between the area corresponding to Haifa Bay (HB) and the zone corresponding to the Southern Israel Coast (SIC). </p>
            <p> The spatial variation of the most abundant taxa, i.e. the taxa with more than 150 individuals in the period 2010-2017, was observed to understand how the species were distributed among the stations (Figure 6). Figure 6 shows the total number of individuals detected per site. Two different assemblages between the two areas (stations “HM” in Haifa Bay vs. stations “H” in Southern Israeli Coast) are evidenced.  Ampelisca spp. was present along the coast of Israel and occasionally close to the Haifa promontory (sites HM27 and H3).  Bathyporeia guilliamsoniana was found along the southern coast of Israel and only sporadically in Haifa Bay in 2014 and 2016-2017; it was very abundant in the southern coastal area, in the region between the Haifa promontory and Tel Aviv (H3-H13), with lower abundances southernmost close to the Israeli desalination plants (sites H19-H24 and H28).  Cheiriphotis mediterranea was found abundant in Haifa Bay and only occasionally along the southern coast of Israel, with a localised discrete amount in the southern coast close to the Israeli desalination plants (sites H19- H24 and H28).  Grandidierella bonnieroides , a species recorded for the first time in 2014 in Haifa Bay, showed sporadic occurrence in other sites.  Megaluropus massiliensis showed a homogeneous distribution along the coast, and higher abundances around the Haifa port sites (HM10 and HM23.1), Tel Aviv (H13), and Ashkelon (H28).  Perioculodes longimanus was consistently present in high abundance along the entire coast of Israel, confirming its tolerance to different conditions.  Photis longicaudata was collected only in the Bay of Haifa, close to the ports, (H2.1 and HM27), and sporadically close to the desalination plants, particularly starting from 2015 (sites H19-H24 and H28).  Urothoe grimaldii was a dominant species along the southern Israeli coast and occasionally in Haifa Bay. </p>
            <p> The spatial distribution of the most abundant taxa and granulometry dataset was analysed through a principal component analysis (PCA). A substantial diversity was scored between Haifa Bay Port (HM27) and Haifa Bay harbour (HM2.1) sites and the other stations (Figure 7). The PCA plot indicates significant site discrepancy (Figure 7). The first two PCA axes explained respectively the 83.1 and 9.6 % of the total variation. The first principal component separated the sites based on the relevant presence of  Cheiriphotis mediterranea +  Photis longicaudata species in Haifa Bay (HM2.1 and HM27) (see also Figure 6) and the gravel/coarse sediment. The second principal component distinguished the sites due to the presence of  Bathyporeia guilliamsoniana +  Perioculodes longimanus +  Urothoe grimaldii assemblage (see also Figure 6) and the fine sand sediment. </p>
            <p>Discussion</p>
            <p>Marine biodiversity changes across spatial and temporal scales and the extent of such changes can depend on the context and the taxon investigated (Steger et al. 2024). In this paper, a monitoring survey along the Israeli coast provided an example of what a multiscale approach can reveal.</p>
            <p>A study of the Israeli amphipod fauna – a dominant taxon of the marine ecosystems – was conducted along the coast on the soft littoral bottom area for eight years. This was the first temporal quantitative study performed on the benthic amphipod fauna in the country. Twenty-five taxa (species or genera) were recorded from a sampling effort in the same stations, located in the northernmost Haifa Bay and along the southern coast, at the same depth range.</p>
            <p>The dataset showed an overall stable assemblage of the most common species, with sporadic records of occasional species usually associated with macroalgae or seagrasses reaching very low abundances, generally, less than 150 individuals or detected once over the eight years.</p>
            <p> Seven species showed the highest abundances and a temporally constant presence: the Levantine endemic  Cheiriphotis mediterranea ; the Mediterranean endemic  Megaluropus massiliensis ; the NE Atlantic–Mediterranean  Bathyporeia guilliamsoniana and  Perioculodes longimanus ; and  Photis longicaudata and  Urothoe grimaldii presumably widely distributed in the Atlantic Ocean, the Mediterranean Sea and the Indian Ocean. The most significant change was the detection of an alien species in 2014, the circumtropical aorid  Grandidierella bonnieroides which resulted naturalized (Lo Brutto et al. 2016). </p>
            <p> This is not the only Non-Indigenous (NIS) amphipod species detected in Israeli waters; Bemblos leptocheirus, and  Paracaprella pusilla were documented in the region at different sites not included in the present paper (Lo Brutto et al., 2019; Lo Brutto and Iaciofano, 2020). </p>
            <p> The abundance of these seven species was observed to be unstable at the local level, as fluctuations occurred in the different stations. The range of abundance fluctuations was considerable, encompassing peaks of high numbers of individuals concentrated in specific years which differed among the species; for instance,  Cheriphotis mediterranea reached 1805 individuals in station HM2.1 in 2014. No correlation was observed between the total abundance per site and year and the species richness, as the fluctuating abundances were attributable to the few dominant species and the assemblages showed a low α- diversity. </p>
            <p>The random fluctuations mirrored the ecological traits of the species (Navarro-Barranco et al., 2017). The taxa identified in the present study can be classified as hyperbenthos, representing the predominant benthic boundary layer faunal component. The inhabitants of the water layer adjacent to the seabed feed on organic particles on the bottom and, at the same time, are capable of vertical migrations, playing a significant trophic role in the benthic communities and within water column food webs (Buhl-Jensen and Fosså, 1991; Koulouri et al., 2013). These features made the species influenceable by anthropogenic drivers impacting the littoral communities such as nutrient enrichment.</p>
            <p> The taxocenosis observed was characterised by deposit feeders on the surface of the bottom, such as ampeliscids,  Bathyporeia and  Urothoe genus, and species able to perform vertical migrations, such as  B. guilliamsoniana ,  M. massiliensis and  P. longimanus . However, a long-temporal variation in the faunal structure which was expected due to the increase of anthropogenic and environmental stressors was not observed. </p>
            <p> The analyses detected only a significant spatial variation that discriminated Haifa   Bay from the  Southern Israeli Coast  . </p>
            <p>The physical features of the sediment frequently play a crucial role in shaping amphipod assemblage structure (Buhl-Jensen &amp; Fosså, 1991; Fanelli et al., 2011; de-la-Ossa-Carretero et al., 2012; Scipione, 2013). Along Israeli coast, the bottom, in terms of sediment grain size and chemical composition (Lubinevsky et al., 2019), displayed two areas of different substratum, with which amphipods were associated. Haifa Bay area was more polluted and eutrophic and with a higher portion of gravel, and coarse and medium sand than the Southern Israeli Coast (Lubinevsky et al., 2019). As a consequence, the seven most abundant species were spatially distributed according to the type of sediment that favoured their feeding habit. The different species compositions between the two areas reflected the local environmental features.</p>
            <p> The information about the sensitivity of the dominant species to disturbances is worthy of remarks. According to de-la-Ossa-Carretero et al. (2012) shallow soft-bottom amphipods can show different sensitivity levels due to their burrowing behaviour; fossorial can show higher sensitivity than domicolous species. This prediction is confirmed in the present paper. Fossorial species, such as  Bathyporeia guilliamsoniana ,  Perioculodes longimanus , and particularly  Urothoe grimaldii (Scipione, 2013) , showed a negative response to polluted stations, where they reduced their abundance; other fossorial species showed an unclear pattern or, indeed, a certain tolerance such as  Megaluropus massiliensis , previously indicated as sensitive to polluted areas (Çinar et al., 2015) and present here with the high abundances around the Haifa harbour localities. The domicolous filter feeders  Cheiriphotis mediterranea and  Photis longicaudata (Scipione, 2013) characterized the gravel/coarse sediment stations in Haifa Bay, an area which receives pollutants from rivers effluent of chemical and petrochemical industries, urban and agricultural runoff, and from the Haifa municipality domestic sewage treatment plants. </p>
            <p> The dataset also provided biogeographical information on certain species that, to date, appear to exhibit a wide geographic distribution, including  U. grimaldii and  P. longimanus , the latter of which was unexpectedly documented from the Barents Sea to New Zealand. These geographical ranges must be subjected to rigorous examination and verification, as it is highly improbable that some of these species can be found in areas that are geographically distant or in habitats with markedly dissimilar environmental characteristics.  Urothoe grimaldii , a species typically found in sandy habitats, was documented as an epibiont of loggerhead sea turtles (Zakhama-Sraieb et al., 2009). Similarly,  P. longimanus was reported in the literature as both an infralittoral and bathyal species (Cartes et al., 2007). The present paper shows that the benthic fauna in Israeli coastal marine environments has not changed over time, showing a pattern congruent with long-term analyses of other taxa (molluscs in Steger et al., 2024). Considering the low species richness, changes in amphipod assemblages are expected to be particularly evident if they occur in the future. In this respect, this comprehensive dataset contributes to our knowledge of the Levantine area and its fauna. Data extrapolated from a long time series provide an accurate baseline for detecting putative changes in biodiversity, and a precise understanding of species distributions is essential for monitoring the impact of climate change on marine ecosystems. </p>
            <p>Acknowledgments</p>
            <p>Financial support was provided by the Department DiSTeM of the University of Palermo and by the National Recovery and Resilience Plan (NRRP), Mission 4 Component 2 Investment 1.4 - Call for tender No. 3138 of 16 December 2021, rectified by Decree n.3175 of 18 December 2021 of Italian Ministry of University and Research funded by the European Union – Next Generation EU. Project code CN_00000033, Concession Decree No. 1034 of 17 June 2022 adopted by the Italian Ministry of University and Research, CUP D33C22000960007, Project title “National Biodiversity Future Center - NBFC”. The authors are grateful to Bella Galil for providing some samples included in the study and Beatrice Scipione for the interesting discussion aimed at improving the manuscript.</p>
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            <p>Supplementary material</p>
            <p>SIMPER analyses</p>
            <p>Data type: pdf</p>
            <p>Link: https://www.biotaxa.org/em/article/view/86645/81352</p>
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	https://treatment.plazi.org/id/03E97B2DFFF4587B6030FAD9FC73CE1F	Public Domain	No known copyright restrictions apply. See Agosti, D., Egloff, W., 2009. Taxonomic information exchange and copyright: the Plazi approach. BMC Research Notes 2009, 2:53 for further explanation.		Plazi	Iaciofano, Davide;Mancini, Emanuele;Lubinevsky, Hadas;Brutto, Sabrina Lo	Iaciofano, Davide, Mancini, Emanuele, Lubinevsky, Hadas, Brutto, Sabrina Lo (2024): The amphipod fauna assemblage along the Mediterranean Israeli coast, a spatiotemporal overview. Ecologica Montenegrina 80: 244-272, DOI: 10.37828/em.2024.80.22, URL: https://doi.org/10.37828/em.2024.80.22
