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1. The Mediterranean starry ray (Raja asterias) populations within the Mediterranean Sea are susceptible to high rates of bycatch in the multispecies trawl fisheries. Understanding its population structure and identifying critical habitats are crucial for assessing species vulnerability and setting the groundwork for specific management measures to prevent population decline. 2. To assess the population structure of R. asterias in the Mediterranean, the genetic variation in nine population samples at one mitochondrial marker and eight nuclear microsatellite loci was analysed. Moreover, 172 egg cases collected in the Strait of Sicily were identified at species level using integrated molecular and morphological approaches. 3. Genetic analyses revealed that the Mediterranean starry ray comprises three distinct units inhabiting the western, the central-western, and the central-eastern areas of the Mediterranean. An admixture zone occurs in the Strait of Sicily and the Ionian Sea, where individuals of the central-western and central-eastern population units intermingle. 4. The joint morphometric–genetic analyses of rajid egg cases confirmed the presence of more than one species in the admixture area, with a predominance of egg cases laid by R. asterias. DNA barcoding revealed that egg cases and embryos of R. asterias shared several haplotypes with adult individuals from the centralwestern and central-eastern Mediterranean Sea, revealing that females of both populations laid numerous eggs in this area. 5. According to these findings, detailed taxonomic determination of egg cases, when combined with seasonal migration studies, could improve the capability to identify important spawning or nursery areas for the Mediterranean starry ray, particularly in those admixture zones relevant to maintaining genetic diversity. 6. Finally, these new insights should be considered to update the Action Plan for the Conservation of Cartilaginous Fishes in the Mediterranean Sea with effective measures to reduce the impact of skate bycatch in trawling and safeguard egg cases in nursery areas.

Centrophorus uyato (Rafinesque, 1810) Little Gulper Shark Synonymy. Dalatias nocturnus Rafinesque, 1810: 11, pl. 14, fig. 3 (Type locality: Sicily, Italy)— Cuvier, 1818: 455; Cuvier, 1829: 392; Cuvier, 1837: 246; Swainson, 1838: 129, 160; Swainson, 1839: 313; Duméril, 1865: 436; Jordan & Evermann, 1917: 77; Bigelow & Schroeder, 1948: 500. Spinax uyatus — Bonaparte, 1834: 49, fig. 2 (Italy); Bonaparte, 1846: 16 (Mediterranean); Böhlke, 1984: 158. Acanthias uyatus — Müller & Henle, 1839: 85 (Mediterranean); Gray, 1851: vii, 71 (Mediterranean); Steindachner, 1864: 27; Duméril, 1865: 439 (Algerian coast, Mediterranean); Barbosa du Bocage & de Brito Capello, 1866: 7, 21; Günther, 1870: 419 (Mediterranean); Canestrini, 1872: 40; Steindachner, 1875: 466; Moreau, 1881: 346 (Mediterranean); Réguis, 1882: 72; Rochebrune, 1883: 47 (Senegal and Gambia); Hilgendorf, 1884: 518; Duncan, 1891: 35 (Mediterranean); Moreau, 1892: 39; Seeley, 1895: 35 (Mediterranean); Parona, 1898: 38 (Ligurian Sea); Duncker, 1914: 291; de Buen, 1916: 303, figs (Mediterranean coast of Morocco); Landolt, 1947: 353. Centrophorus granulosus — Müller & Henle, 1839: 89, pl. 33 (Sicily, Italy); Barbosa du Bocage & de Brito Capello, 1864: 261 (Portugal); Vinciguerra, 1883: 18 (482) (Gulf of Genoa); Goode & Bean, 1896: 12, pl. 3, fig. 11 (W Atlantic, Mediterranean and adjacent areas); Boutan, 1926: 1 (Algeria); Dieuzeide, 1928a: 15, figs (Algeria); Dieuzeide, 1928b: 1314 (Algeria?); Andr & Canal, 1929: 511 (Algeria); Arcidiacono, 1931: 609 (Gulf of Squillace, Italy); Gruvel, 1931: 74 (State of Syria [Syria, Lebanon, Israel]); Ranzi, 1932: 240 (Naples, Italy); Belloc, 1934: 146, fig. (Western Sahara, Morocco, Canary Islands and Madeira); Ranzi, 1934: 343, 370 (Naples, Italy); Fowler, 1936: 73 (Mediterranean); Fowler, 1941 (in part): 231 (Mediterranean, inc. Italy); Šoljan, 1948: 66, figs (Adriatic Sea); Bigelow et al., 1955: 6 (Gulf of Mexico); Kirinčić & Lepetić, 1955: 24 (southern Adriatic Sea); Tortonese, 1956: 176, figs 94-95 (Italy); Cadenat, 1959: 748, fig. 1b (West Africa); Maurin, 1968: 82 (Morocco to Algeria); Maurin & Bonnet, 1970: 147 (Canary Islands to Cape Verde); Karrer, 1975: 64 (Namibia); Karlovac, 1976: 601, fig. 4 (Adriatic Sea); Guitart, 1979: 67, fig. 46 (Cuba); Bouchet et al., 1982: 577 (Tunisia); Zupanovic & El-Buni, 1982: 111 (Libya); Uyeno et al., 1983: 62, figs (Suriname); Compagno, 1984a: 37, figs (Atlantic and Indo-West Pacific); Gilat & Gelman, 1984: 263 (Levant Sea, Israel); McEachran & Branstetter, 1984: 130, fig. (NE Atlantic and Mediterranean); Muñoz-Chapuli, 1984: 9 (NE Atlantic);? Quéro, 1984: 43, fig.; Capapé, 1985: 97, fig. 1–7 (Eastern Atlantic); Jardas, 1985: 50 (Adriatic Sea); Anon, 1986: 93, fig. 22 (Atlantic Ocean); Bass et al., 1986 (in part): 50, fig. 5.1 (Walvis Bay and Mozambique); Golani, 1986: 23, fig. 2 (Levantine Sea, Israel); Muñoz-Chapuli & Ramos, 1989: 65, figs 1a, 3a, 4b and c, 5a, 6a, 7a (NE Atlantic and Mediterranean); Compagno et al., 1991: 54 (Hondeklip Bay to Namibia); Benli et al., 1993: 133, figs 1 and 2 (Sea of Marmara); Pisanty & Golani, 1995: 388 (Levantine Sea, Israel); Lanfranco, 1996: 6, pl. 4 (Malta); Aldebert, 1997: 284 (Gulf of Lion, France); Guallart, 1998: 1, figs (Balearic Sea); Bello, 1999: 69 (Adriatic Sea); Hernández-Hamón & Núñez, 1998: 107 (Pacific Columbia); Ungaro et al., 1999: 180 (Albania); Capapé et al., 2000: 129 (Languedoc coast, France); Bertrand et al., 2000: 5 (Gibraltar to Aegean Sea, Mediterranean); Golani & Pisanty, 2000: 71 (Levantine Sea, Israel); Baino et al., 2001: 234 (Alboran Island to Aegean Sea, Mediterranean); Guallart & Vicent, 2001: 135, fig. 4 (Balearic Sea, Spain); Bilecenoglu et al., 2002: 16 (Turkey); Schembri et al., 2003: 76, fig. 3c (Malta); McLaughlin & Morrissey, 2004: 481, fig. 3 (Cayman Trench, Jamaica); Moreno García, 2004: 214 (in part, not figs) (Mediterranean Sea); Sion et al., 2004: 155 (Ionian Sea, Greece); Golani, 2005: 11 (Levantine Sea, Israel); Lteif, 2015: 16, figs 9a, 14, (Lebanon); Serena, 2005: 27, figs, pl. I, 8 (Mediterranean Sea); Serét, 2005: 21 (Libya); Bessho, 2006: 28, figs 27–30, 33–35 (Japan, Namibia); Golani et al., 2006: 38, fig. (eastern Mediterranean); Hadjichristophorou, 2006: 163 (Cyprus); Megalofonou & Chatzispyrou, 2006: 67, fig. 4 (Crete, Greece); Mejía-Falla et al., 2007: 116 (Colombia); Psomadakis et al., 2009: 200 (Gulf of Naples, Italy); D’Onghia et al., 2010: 401 (Ionian Sea, Greece); Lipej & Dulĉić, 2010: 10 (Adriatic Sea); Damalas & Vassilopoulou, 2011: 145 (Aegean Sea, Greece); Colloca & Lelli, 2012: 12 (Lebanon); Costa et al., 2012: 7 (Portugal); Guijarro et al., 2012: 89 (Balearic Islands, Spain); Güven et al., 2012: 278 (Antalya Bay, Turkey); Iglésias, 2013: 38, pl. 16 (France and Cape Verde); Carneiro et al., 2014: 13 (Portugal); Farrugio & Soldo, 2014: 33 (Sicily, Italy and Tunisia); Veríssimo et al., 2014: 6 (Gulf of Mexico); Goren & Galil, 2015: 510 (Levant Sea, Israel); Barría et al., 2015a: 226 (Catalan Sea, Spain and Gulf of Lions, France); Barría et al., 2015b: 114 (Catalan Sea, Spain and Gulf of Lions, France); Carpenter & De Angelis, 2016: 1170, figs (Eastern Atlantic); Ramírez-Amaro et al., 2016: 639 (western Mediterranean); Cariani et al., 2017: 5 (Mediterranean);? Haroun et al., 2017: 84 (Egypt); Gajić, 2019: 101, fig. 14 (Croatia, Montenegro and Albania); Bariche & Fricke, 2020: 17, fig. 12 (Lebanon). ? Acanthias nigrescens Nardo, 1860: 70, 96 (Type locality: Venice, Italy). Entoxychirus uyatus — Gill, 1862: 498; Whitley, 1934: 199 (Australia). Acanthias ujatus — Döderlein, 1878: 30 (Sicily, Italy); Döderlein, 1881: 92 (Italy). Centrophorus uyatus — Goode & Bean, 1896: 508; Garman, 1906: 204; Garman, 1913: 9, 196. Squalus uyatus — Garman, 1899: 28. Squalus uyato — Garman, 1906: 204. Centrophorus bragancae Regan, 1906: 438 (Type locality: Cezimbra, Portugal)— Regan, 1908: 53 (coast of Portugal); Strand, 1908: 83. Centrophorus uyato — Fowler, 1936: 72, fig. 21 (Mediterranean and eastern Atlantic); Tortonese, 1938: 310 (Mediterranean); Poll 1951: 64, figs 33–34 (Angola and Namibia); Bigelow et al., 1953: 227, fig. 4 (Gulf of Mexico; Nice, Mediterranean Sea); Aksiray, 1954?: 233 (Turkish Seas); Bigelow et al., 1955: 5, 9; Springer & Bullis, 1956: 42 (Gulf of Mexico); Bigelow & Schroeder, 1957: 54, 66, 69, 72, 79–84, fig. 8e (Gulf of Mexico); Springer & Garrick, 1964: 81, 91; Krefft & Tortonese, 1973: 39 (NE Atlantic and Mediterranean); Bass et al., 1976: 31, figs 22, 24E, 24F, pl. 7 (southern Mozambique); Bridger, 1978: 26 (west of Ireland and Britain); Compagno, 1981: 8 [sharks] (Eastern Central Atlantic); Castro, 1983: 54, figs (Gulf of Mexico); Allu et al., 1984: 125 (Namibia); Compagno, 1984a: 45, figs (Atlantic, Indo-West Pacific); Compagno, 1984b: 9 [sharks] (Western Indian Ocean); McEachran & Branstetter, 1984: 132, fig. (NE Atlantic and Mediterranean); Lloris, 1986: 96, fig 24 (Namibia); Turón et al., 1986: 63 (Namibia); Fischer et al., 1987: 823 (Mediterranean); Compagno, 1988b: 603 (Comoro Islands); Compagno et al., 1989: 24, fig. (Hondeklip Bay, South Africa to Namibia);? Clark & Kristof, 1990: 277, fig. 9 (Caribbean); Springer, 1990: 11 (Gulf of Mexico, Mediterranean, and Natal, South Africa); Applegate et al., 1993: 35 (Atlantic Mexican waters); Gomon et al., 1994: 92, 94, figs 30, 31 (southern Australia); Last & Stevens, 1994: 60, figs, pl. 4 (fig. 8.5) (southern Australia); Meriç, 1995: 192 (Sea of Marmara, Turkey); Perry et al., 1995: 139 (Gulf of Mexico); Reiner, 1996: 22, fig. (Cape Verde); Bonfil, 1997: 105 (Veracruz, Mexico); Joseph, 1999: [unpaginated] (Sri Lanka); Cervigón & Alcalá, 1999 (Venezuela); Clarke, 2000: 377 (Rockall Trough, NE Atlantic); Baino et al., 2001: 234 (Alboran Island to Aegean Sea, Mediterranean); Graham et al., 2001: 551 (south-eastern Australia); Yearsley et al., 2001: 35, 360 (southern Australia); Bilecenoglu et al., 2002: 17 (Turkey); Daley et al., 2002: 53 (southern Australia); Ali & Saad, 2003: 58, fig. (Syria); Schembri et al., 2003: 77, fig. 3d (Malta); Serena, 2005: 28, figs, pl. I, 9 (Mediterranean Sea, NE Atlantic, Western Indian, Gulf of Mexico and Taiwan); Meriç et al., 2007: 31 (Turkey); White, 2008: 87, figs (southern Australia); Scacco et al., 2010: 39, fig. 3f (Mediterranean Sea); Castro, 2011: 81, figs 16a-e (north-western Atlantic); Davenport et al.: 2011: 557 (north-western Atlantic, USA); White et al., 2013: 36, fig. 2, 15, 16 (Atlantic); Veríssimo et al., 2014: 6, fig. 5 (Gulf of Mexico); Hipes, 2015: 1, fig. 11 (Gulf of Mexico, USA); Wienerroither et al., 2015: 834, fig. 2 (northern Norway); Farrag, et al., 2016: 481, fig. 2a (Egypt); Driggers et al., 2017: 52 (Gulf of Mexico); Haroun et al., 2017: 84 (Egypt); Lteif et al., 2017: 1491 (Lebanon); Biscoito et al., 2018: 471, fig. 7 (Madeira, Portugal); Carneiro et al., 2019: 36 (Portugal); Ehemann et al., 2019: 4 (Venezuela); Fernando et al., 2019: 231, figs 5e, 18d-f (Mutur, Sri Lanka); Follesa et al., 2019: 85 (Mediterranean); Psomadakis et al., 2019: 162, figs, pl. X (fig. 70) (Myanmar); Iglésias, 2020: 46, pl. 21 (France and Cape Verde); Ebert & Dando, 2021: 217, figs (NE Atlantic and Mediterranean); Kousteni et al., 2021: 1, figs 2 and 3 (Cypriot waters). Centrophorus machiquensis Maul, 1955: 5, figs 13–16 (Type locality: Madeira)— Krefft & Tortonese, 1973: 39 (Madeira); Ali & Saad, 2003: 57, fig. (Syria); Biscoito et al., 2018: 470, fig. 6 (Madeira, Portugal); Almeida & Biscoito, 2019: 99 (Canary Islands and Madeira); Carneiro et al., 2019: 36 (Portugal). Centrophorus ujato — Tortonese, 1956: 178, fig. 96 (Genova, Italy); Bini, 1967: 97, fig. (Italy); Sara, 1968: 1, figs 1–3 (west of Sicily); FAO, 1971: no pagination (Mediterranean Sea). Centrophorus spp. (granulosus group)— Forster et al, 1970 (in part): 388 (Western Indian Ocean). Centrophorus (forme) uyato-machiquensis — Cadenat & Blache, 1981: 58, figs. 36, 37 and 40 (NE Atlantic). Centrophorus spp. — Peyronel et al., 1984: 643 (Bay of Ajaccio, Corsica, France). Centrophorus cf. harrissoni (Undescribed gulper shark #2)— Kiraly et al., 2003: 2 (Puerto Rico, US Virgin Islands, Virginia, North Carolina and Florida Straits to Dry Tortugas). Centrophorus bragance — Hernández-Hamón & Núñez, 1998: 108 (as questionable synonym of C. granulosus). Centrophorus sp. (uyato ?)— Morón et al., 1998: 144 (Beruwela, Sri Lanka). Centrophorus sp. cf. uyato — Saad, et al., 2004: 430 (Syria). ? Centrophorus sp. (non uyato)— Serét, 2005: 21 (Libya). Centrophorus zeehaani White, Ebert & Compagno, 2008: 1, figs 8-10 (Type locality: South Australia)— Last & Stevens, 2009: 68, pl. 9.7, figs (southern Australia); Pethybridge et al., 2010: 1369 (Tasmania and Great Australian Bight, Australia); Pethybridge et al., 2011: 2743 (Tasmania and Victoria, Australia); Graham & Daley, 2011: 583 (southern Australia); Daley et al., 2012: 708 (southern Australia); White et al., 2013: 41 (southern Australia); Daley et al., 2015:127 (southern Australia); Wienerroither et al., 2015: 834, fig. 2 (northern Norway); Bineesh et al., 2016: 461 (Kollam, India). Centrophorus cf. uyato — McLaughlin & Morrissey, 2005: 1185, figs 2, 3 (Cayman Trench, Jamaica); Veríssimo et al., 2014: 7 (Gulf of Mexico); Serena et al., 2020: 502, 509 (Mediterranean); Bellodi et al., 2022: 2 (Mediterranean Sea). Centrophorus zeehani — Daley et al., 2012: fig. 2 (misspelling; southern Australia); Bineesh et al., 2016: 466 (misspelling; Kollam, India). Centrophorus ‘uyato’ — White et al., 2017: 86 (Eastern Atlantic); Almeida & Biscoito, 2019: 100 (Mediterranean Sea, Canary Islands and Madeira). Centrophorus cf. granulosus — Follesa et al., 2019: 85 (Mediterranean); FAO, 2018: unpaginated, fig. (Mediterranean Sea). ? Centrophorus granulosus — Parenti, 2019: 102 (Sicily). Material examined. Neotype: BMNH 2021.10.4.1 (eviscerated; GenBank accession ON167716), female 983 mm TL, between Gorgona and Capraia islands, Ligurian Sea, 43°19.8′ N, 9°56.1′ E, 180 m, 20 Dec. 2012. Other specimens: Australia: AMS I 44310 –001 (paratype of Centrophorus zeehaani; GenBank accession ON167706), adult male 826 mm TL, southwest of Coffin Bay, South Australia, 35°14′ S, 134°29′ E, 360–600 m, 28 July 2005; CSIRO CA 4104, adult male 843 mm TL, east of Gabo Island, Victoria, 37°40′ S, 150°15′ E, 504–508 m, 4 May 1984; CSIRO H 866–02, immature male 456 mm TL, CSIRO H 867–01, female 439 mm TL, east of Jervis Bay, New South Wales, 34°58′ S, 151°09′ E, 490–576 m, 10 Sep. 1986; CSIRO H 2268–02, adult male 800 mm TL, west of Bunbury, Western Australia, 33°03′ S, 114°25′ E, 701 m, 10 Feb. 1989; CSIRO H 6307–01 (skeletal parts), female 1027 mm TL, 12 July 2004, east of Flinders Island, Tasmania, ~ 40° S, ~ 149° E, 350–430 m; CSIRO H 6309–01 (skeletal parts; GenBank accession ON167708), adult male 865 mm TL, CSIRO H 6309–02 (skeletal parts), adult male 876 mm TL, CSIRO H 6309–04 (skeletal parts), adult male 906 mm TL, east of Flinders Island, Tasmania, ~ 40° S, ~ 149° E, 400–450 m, 1 Aug. 2004; CSIRO H 6310–04 (skeletal parts), female 970 mm TL, northeast of Flinders Island, Tasmania, 39°04′ S, 148°39′ E, 500–680 m, 24 Jul. 1986; CSIRO H 6311–01 (skeletal parts), female 655 mm TL, east of St. Helens, Tasmania, 41°27′ S, 148°44′ E, 850–860 m, 5 Jun. 1987; CSIRO H 6500-02, adult male 862 mm TL, east of Flinders Island, Tasmania, 40°15′ S, 148°45′ E, 329–512 m, 21 Aug. 2003; CSIRO H 6503–02 (skeletal parts), female 991 mm TL, CSIRO H 6503–03 (skeletal parts; GenBank accession ON167709), female 1023 mm TL, CSIRO H 6503–04 (skeletal parts; GenBank accession ON167710), female 987 mm TL, CSIRO H 6503–05 (skeletal parts), female 957 mm TL, northeast of Flinders Island, Tasmania, 39°20′ S, 148°45′ E, 370–420 m, 7 Apr. 2003; CSIRO H 6504–02, adult male 854 mm TL, CSIRO H 6504–03, female 817 mm TL, CSIRO H 6504–04, juvenile male 666 mm TL, CSIRO H 6504–05, adult male 861 mm TL, east of Jervis Bay, New South Wales, 35°12′ S, 150°58′ E, 320–500 m, July to Aug. 2003; CSIRO H 6628–01 (paratype of Centrophorus zeehaani), immature male 506 mm TL, CSIRO H 6628–02 (paratype of Centrophorus zeehaani; GenBank accession ON167705), immature male 645 mm TL, CSIRO H 6628–03 (paratype of Centrophorus zeehaani), adult male 875 mm TL, CSIRO H 6628–04 (paratype of Centrophorus zeehaani), adult male 910 mm TL, CSIRO H 6628–05 (holotype of Centrophorus zeehaani), adult male 893 mm TL, CSIRO H 6628–06 (paratype of Centrophorus zeehaani), adult male 852 mm TL, CSIRO H 6628–07 (paratype of Centrophorus zeehaani), adult male 906 mm TL, NMV A 29736 –001 (paratype of Centrophorus zeehaani), adult male 820 mm TL, southwest of Coffin Bay, South Australia, 35°14′ S, 134°29′ E, 360–600 m, 28 July 2005; CSIRO unreg. (DB 02/181), Great Australian Bight, adult male 857 mm TL; CSIRO unreg. (LJVC 880517), female 840 mm TL, unknown location; PMH095-11 (jaws only), female 104 cm TL, Albany, Western Australia. Eastern Atlantic (including Mediterranean): AMNH 78267, female 922 mm TL, AMNH 78269, female 937 mm TL, AMNH 78271, female 1016 mm TL, AMNH 78273, adult male 872 mm TL, AMNH 78277, adult male 895 mm TL, AMNH 78279, adult male 890 mm TL, between Tenerife and Gran Canaria, Canary Islands, Spain, 3 Oct. 1986; AMNH 78280, female 996 mm TL, AMNH 78282, female 1059 mm TL, AMNH 78283, female 1056 mm TL, AMNH 78284, adult male 832 mm TL, AMNH 78285, female 921 mm TL, AMNH 78286, female 1004 mm TL, AMNH 78291, female 1034 mm TL, AMNH 78292, female 980 mm TL, AMNH 78294, adult male 891 mm TL, between Tenerife and Gran Canaria, Canary Islands, Spain, 4 Oct. 1986; BMNH 1862.4.22.29, female 449 mm TL, Madeira, Portugal; BMNH 1864.7.18.1, female 894 mm TL, Madeira, Portugal; BMNH 1904.11.30.9- 10 (2 specimens), female 1036 mm TL, adult male 888 mm TL, west of Faro, Portugal, 662 m depth; BMNH 1904.11.30.11 (paralectotype of Centrophorus bragancae), juvenile male 488 mm TL, off Sesimbra, Portugal, 841 m depth; BMNH 1904.11.30.12 (lectotype of Centrophorus bragancae), female 467.5 mm TL, off Sesimbra, Portugal, 505 m depth; BMNH 2013.9.20.34, female 875 mm TL, BMNH 2013.9.20.35, female 930 mm TL, BMNH 2013.9.20.36, female 935 mm TL, BMNH 2013.9.20.37, female 731 mm TL, BMNH 2013.9.20.38, adult male 843 mm TL, BMNH 2013.9.20.39, adult male 865 mm TL, northeast Atlantic; CSIRO H 7471-01 (GenBank accession ON167715), adult male 853 mm TL, east of Corsica, France, 42°05.8′ N, 9°44.5′ E, 550–565 m, 30 May 2012; CSIRO H 7472-01, juvenile male 440 mm TL, southeast of Corsica, France, 41°47.9′ N, 9°30.5′ E, 466–480 m, 31 May 2012; ERB 1288, male 770 mm TL, Concarneau fish-market, France, 9 Sep. 2000; ERB 0763, male, 850 mm TL, Concarneau, France, 13 May 2009; HUJ 10885, female 760 mm TL, Hadera, Israel, 13 Sep. 1982; HUJ 11339, adult male 796 mm TL, Haifa Bay, Israel, 1 Mar. 1983; HUJ 17029, female 476 mm TL, Haifa, Israel, 16 Mar. 1983; HUMZ 151304, juvenile male 578 mm TL; HUMZ 151306, female 978 mm TL, Namibia; HUJ 21135 (GenBank accession ON167718), female 753 mm TL, Haifa fishing port, Israel, 29 July 2013; MNHN-IC 1905- 0568, juvenile male 454 mm TL, Portugal, 460 m depth, June 1903; MNHN-IC 1969-0269, juvenile male 499 mm TL, southwest of Monrovia, Liberia, 6°08′ N, 10°56′ W, 400 m depth, 27 Apr. 1964; MNHN-IC 0000-1224, female 537 mm TL, Naples, Italy; MNHN-IC 2005-0169, adult male 892 mm TL, west of Ireland, 28 Apr. 2005; NMW 15009, female 889 mm TL, Nice; NMW 63020, adult male 880 mm TL, Nice, France, 1902, Published as part of White, William T., Guallart, Javier, Ebert, David A., Naylor, Gavin J. P., Mo, Ana Veríssi-, Cotton, Charles F., Harris, Mark, Serena, Fabrizio & Iglésias, Samuel P., 2022, Revision of the genus Centrophorus (Squaliformes: Centrophoridae): Part 3 - Redescription of Centrophorus uyato (Rafinesque) with a discussion of its complicated nomenclatural history, pp. 1-51 in Zootaxa 5155 (1) on pages 15-41, DOI: 10.11646/zootaxa.5155.1.1, http://zenodo.org/record/6669082, {"references": ["Rafinesque, C. S. (1810) Caratteri di alcuni nuovi generi e nuove specie di animali e piante della Sicilia, con varie osservazioni sopra i medisimi. Sanfilippo, Palermo, 1, 3 - 69. https: // doi. org / 10.5962 / bhl. title. 104418", "Cuvier, G. (1818) Dictionnaire des sciences naturelles, dans lequel on traite meithodiquement des diffeirens e \u02c6 tres de la nature, consideireis soit en eux-me \u02c6 mes, d'apreIs l'eitat actuel de nos connoissances, soit relativement aI l'utilitei qu'en peuvent retirer la meidecine, l'agriculture, le commerce et les artes. 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Il contributo analizza i modi in cui gli stakeholders sono coinvolti nelle attività di ricerca sulle scienze sociali (SS) finanziate nell'ambito di progetti europei, al fine di identificare elementi - caratteristiche organizzative del progetto, tipi di stakeholder, tipo di coinvolgimento - che possono aumentare la probabilità di produrre un impatto sulla politica e sulla società; ven-gono inoltre discusse le conseguenze delle evidenze empiriche per la valutazione della ricerca.

This chapter describes the methodology of the CNR-IRCrES survey, conducted to investigate the effects of agile working emergency implementation on the research personnel from two Italian Public Research Organizations - the National Research Council (CNR) and the National Institute for Astrophysics (INAF). This survey, based on the CAWI methodology, sought to explore specific aspects of scientific work such as autonomy, creativity and productivity, as well as contextual aspects such as personal well-being, the use of ICT tools and the environmental implications of agile working. The first part of the chapter describes how the survey was designed and the various dimensions that were investigated by the questionnaire. The second part summarizes the implementation phase while also introducing the participants' profile through a descriptive analysis of the sample of respondents.

With the outbreak of the COVID-19 pandemic, the Italian public administration had to resort to a massive activation of agile working in a situation characterized by chronic delays in widespread adoption of ICT solutions, as well as a state of inertia in providing adequate training for staff on the use of technological services. While organizations attempted to respond to the emergency by providing new tools and services for remote work, many employees, at least in the first phase, were forced to deal with the skills acquired independently in order to use ICT services available and seek solutions to any technical or operational problems. Even knowledge workers, who are highly qualified and potentially predisposed to autonomous and innovative ways of performing research activities, had to adapt to new work dynamics characterized by an increased use of ICTs. This contribution aims to describe the mode and intensity of use of ICT services and tools by nonacademic research personnel during agile working performed in emergency. The interest is primarily focused on the individual early adoption or increased use of ICT resources in response to out-of-office working conditions, regardless of the degree of physical IT equipment eventually provided by organizations. The investigation focuses on the following topics: i) the research personnel's approach to using ICTs for agile working, taking into account individual and organizational preparation; ii) the use experience of ICT tools and services during agile working, enlightening which of them could have played a potentially transformative role in the organization of work; and iii) the main obstacles they encountered in using ICTs in agile working.

This chapter wants to shed light on the value of the autonomy in the organization of the individual work, with respect to the production of new scientific knowledge in non-university research institutions. The empirical base is the experience of smart working implemented in the Public Research Organizations (PROs) during the COVID-19 pandemic emergency, and the individual adaptation/reaction of the research personnel in two Italian PROs: the National Research Council (CNR) and the National Institute for Astrophysics (INAF). During the health-emergency period, scholars were required to work for most of the time at home, and several restrictions on free movement of people were imposed. The aim of this paper is to understand how this special condition influenced the activities of researchers and technologists and the production of original research work, thus impacting positively or negatively their creativity -namely, their attitudes of going beyond the exploitation of existing capabilities and routines.

Recognizing the imperative to evaluate species recovery and conservation impact, in 2012 the International Union for Conservation of Nature (IUCN) called for development of a "Green List of Species" (now the IUCN Green Status of Species). A draft Green Status framework for assessing species' progress toward recovery, published in 2018, proposed 2 separate but interlinked components: a standardized method (i.e., measurement against benchmarks of species' viability, functionality, and preimpact distribution) to determine current species recovery status (herein species recovery score) and application of that method to estimate past and potential future impacts of conservation based on 4 metrics (conservation legacy, conservation dependence, conservation gain, and recovery potential). We tested the framework with 181 species representing diverse taxa, life histories, biomes, and IUCN Red List categories (extinction risk). Based on the observed distribution of species' recovery scores, we propose the following species recovery categories: fully recovered, slightly depleted, moderately depleted, largely depleted, critically depleted, extinct in the wild, and indeterminate. Fifty-nine percent of tested species were considered largely or critically depleted. Although there was a negative relationship between extinction risk and species recovery score, variation was considerable. Some species in lower risk categories were assessed as farther from recovery than those at higher risk. This emphasizes that species recovery is conceptually different from extinction risk and reinforces the utility of the IUCN Green Status of Species to more fully understand species conservation status. Although extinction risk did not predict conservation legacy, conservation dependence, or conservation gain, it was positively correlated with recovery potential. Only 1.7% of tested species were categorized as zero across all 4 of these conservation impact metrics, indicating that conservation has, or will, play a role in improving or maintaining species status for the vast majority of these species. Based on our results, we devised an updated assessment framework that introduces the option of using a dynamic baseline to assess future impacts of conservation over the short term to avoid misleading results which were generated in a small number of cases, and redefines short term as 10 years to better align with conservation planning. These changes are reflected in the IUCN Green Status of Species Standard.

The Mediterranean Large Elasmobranchs Monitoring (MEDLEM) database contains more than 3,000 records (with more than 4,000 individuals) of large elasmobranch species from 21 different countries around the Mediterranean and Black seas, observed from 1666 to 2017. The principal species included in the archive are the devil ray (1,868 individuals), the basking shark (935 individuals), the blue shark (622 individuals), and the great white shark (342 individuals). In the last decades, other species such as the thresher shark (187 individuals), the shortfin mako (180 individuals), and the spiny butterfly ray (138) were reported with increasing frequency. This was possibly due to increased public awareness on the conservation status of sharks, and the consequent development of new monitoring programs. MEDLEM does not have homogeneous reporting coverage throughout the Mediterranean and Black seas and it should be considered as a database of observed species presence. Scientific monitoring efforts in the south-eastern Mediterranean and Black seas are generally lower than in the northern sectors and the absence of some species in our database does not imply their actual absence in these regions. However,the available data allowed us to analyse the frequency and spatial distribution of records, the size frequencies for a few selected species, the overall area coverage, and which species are involved as bycatch by different fishing gears., Sí

Background: We are witnessing increasing demand from governments and society for all sciences to have relevant social impact and to show the returns they provide to society. Aims and objectives: This paper reports strategies that promote social impact by Social Sciences and Humanities (SSH) research projects. Methods: An in-depth analysis of six Social Sciences and Humanities research projects that achieved social impact was carried out to identify those strategies. For each case study, project documents were analysed and qualitative fieldwork was conducted with diverse agents, including researchers, stakeholders and end-users, with a communicative orientation. Findings: The strategies that were identified as contributing to achieving social impact include a clear focus of the project on social impact and the definition of an active strategy for achieving it; a meaningful involvement of stakeholders and end-users throughout the project lifespan, including local organisations, underprivileged end-users, and policy makers who not only are recipients of knowledge generated by the research projects but participate in the co-creation of knowledge; coordination between projects' and stakeholders' activities; and dissemination activities that show useful evidence and are oriented toward creating space for public deliberation with a diverse public. Discussion and conclusions: The strategies identified can enhance the social impact of Social Sciences and Humanities research. Furthermore, gathering related data, such as collaboration with stakeholders, use of projects' findings and the effects of their implementation, could allow researchers to track the social impact of the projects and enhance the evaluation of research impact. Key messages o The social impact of SSH projects is amplified via a focus and an active strategy for achieving it. o The social impact of SSH research is enhanced by meaningful involvement of stakeholders and end-users. o Dissemination leading to social impact is evidence-based, useful, involves beneficiaries and allows debate. o Tracking the social impact of projects could enhance the evaluation of the impact of research.

Marine litter is one of the main sources of anthropogenic pollution in the marine ecosystem, with plastic representing a global threat. This paper aims to assess the spatial distribution of plastic macro-litter on the seafloor, identifying accumulation hotspots at a northern Mediterranean scale. Density indices (items km–2) from the MEDITS trawl surveys (years 2013-2015) were modelled by generalized additive models using a Delta-type approach and several covariates: latitude, longitude, depth, seafloor slope, surface oceanographic currents and distances from main ports. To set thresholds for the identification of accumulation areas, the percentiles (85th, 90th and 95th) of the plastic spatial density distribution were computed on the raster data. In the northern Mediterranean marine macro-litter was widespread (90.13% of the 1279 surveyed stations), with plastic by far the most recurrent category. The prediction map of the plastic density highlighted accumulation areas (85th, 90th and 95th percentiles of the distribution, respectively, corresponding to 147, 196 and 316 items km–2) in the Gulf of Lions, eastern Corsica, the eastern Adriatic Sea, the Argo-Saronic region and waters around southern Cyprus. Maximum densities were predicted in correspondence to the shallower depths and in proximity to populated areas (distance from the ports). Surface currents and local water circulation with cyclonic and anticyclonic eddies were identified as drivers likely facilitating the sinking to the bottoms of floating debris., La basura marina es una de las principales fuentes de contaminación antropogénica en el ecosistema marino representando el plástico una amenaza global. El objetivo de este trabajo es evaluar la distribución espacial de las macro-basuras plásticas en el fondo marino, identificando los hotspots de acumulación en el Mediterráneo norte. Los índices de densidad (ítems km–2), procedentes de las campañas de arrastre MEDITS (años: 2013-2015), fueron modelados mediante Modelos Aditivos Generalizados, utilizando un enfoque de tipo delta y varias covariables: latitud, longitud, profundidad, pendiente del fondo marino, corrientes marinas y distancias desde los principales puertos. Para establecer los umbrales para la identificación de áreas de acumulación, se calcularon los percentiles (85-90-95) de la distribución espacial de densidad de plásticos en los datos ráster. En el Mediterráneo norte, la macro-basura marina estaba muy extendida (90.13% de las 1279 estaciones muestreadas), siendo el plástico, con diferencia, la categoría más recurrente. El mapa de predicción de la densidad de plásticos resaltó las áreas de acumulación (percentiles 85, 90 y 95 de la distribución, respectivamente, correspondientes a: 147, 196 y 316 ítems km–2), localizadas en el Golfo de León, Córcega oriental, Mar Adriático oriental, región Argo-Saronic y aguas que rodean el sur de Chipre. Se predijeron las densidades máximas a menor profundidad y cercanas a zonas pobladas (distancia desde los puertos). Las corrientes superficiales y la circulación local del agua, con giros ciclónicos y anticiclónicos, se identificaron como factores que favorecen el hundimiento de las basuras flotantes.

Thanks to the availability of the MEDITS survey data, a standardized picture of the occurrence and abundance of demersal Chondrichthyes in the northern Mediterranean has been obtained. During the spring-summer period between 2012 and 2015, 41 Chondrichthyes, including 18 sharks (5 orders and 11 families), 22 batoids (3 orders and 4 families) and 1 chimaera, were detected from several geographical sub-areas (GSAs) established by the General Fisheries Commission for the Mediterranean. Batoids had a preferential distribution on the continental shelf (10-200 m depth), while shark species were more frequent on the slope (200-800 m depth). Only three species, the Carcharhiniformes Galeus melastomus and Scyliorhinus canicula and the Torpediniformes Torpedo marmorata were caught in all GSAs studied. On the continental shelf, the Rajidae family was the most abundant, being represented in primis by Raja clavata and then by R. miraletus, R. polystigma and R. asterias. The slope was characterized by the prevalence of G. melastomus in all GSAs, followed by S. canicula, E. spinax and Squalus blainville. Areas under higher fishing pressure, such as the Adriatic Sea and the Spanish coast (with the exception of the Balearic Islands), show a low abundance of chondrichthyans, but other areas with a high level of fishing pressure, such as southwestern Sicily, show a high abundance, suggesting that other environmental drivers work together with fishing pressure to shape their distribution. Results of generalized additive models highlighted that depth is one of the most important environmental drivers influencing the distribution of both batoid and shark species, although temperature also showed a significant influence on their distribution. The approach explored in this work shows the possibility of producing maps modelling the distribution of demersal chondrichthyans in the Mediterranean that are useful for the management and conservation of these species at a regional scale. However, because of the vulnerability of these species to fishing exploitation, fishing pressure should be further incorporated in these models in addition to these environmental drivers., Gracias a la disponibilidad de los datos de campañas de pesca experimental MEDITS, se ha realizado una imagen estandarizada de la presencia y abundancia de Chondrichthyes demersales en el norte del Mediterráneo. Durante el período primavera-verano entre 2012 y 2015, se detectaron 41 Chondrichthyes, incluidos 18 tiburones (5 órdenes y 11 familias), 22 batoides (3 órdenes y 4 familias) y 1 quimera, de varias Subáreas Geográficas (GSA) establecidas por la Comisión General de Pesca para el Mediterráneo en la zona. Los batoides tuvieron una distribución preferencial en la plataforma continental (10-200 m de profundidad), mientras que las especies de tiburones fueron más frecuentes en la ladera (200-800 m de profundidad). Solo tres especies, Carcharhiniformes Galeus melastomus, Scyliorhinus canicula y Torpediniformes Torpedo marmorata fueron capturadas en todos los GSA estudiados. En la plataforma continental, la familia Rajidae fue la más abundante, representada en primer lugar por Raja clavata y luego por R. miraletus, R. polystigma y R. asterias. La pendiente se caracterizó por la prevalencia de G. melastomus en todos los GSA, seguido de S. canicula, E. spinax y Squalus blainville. Las áreas bajo mayor presión de pesca, como el Mar Adriático y la costa española (con la excepción de las Islas Baleares), registran una baja abundancia de condricthianos, pero otras áreas con un alto nivel de presión de pesca, como el suroeste de Sicilia, presentan una gran abundancia de estas especies. Sugiere que otros impulsores ambientales trabajen juntos con la presión pesquera para dar forma a su distribución. Los resultados de los modelos aditivos generalizados resaltaron que la profundidad es uno de los factores ambientales más importantes que influyen en la distribución de las especies de batoides y tiburones, aunque la temperatura también mostró una influencia significativa en su distribución. El enfoque explorado en este trabajo muestra la posibilidad de producir mapas que modelen la distribución de los condrictios demersales en el Mediterráneo, útiles para el manejo y la conservación de estas especies a escala regional. Sin embargo, teniendo en cuenta la vulnerabilidad de estas especies a la explotación pesquera, la presión pesquera debería incorporarse a estos modelos, además de estos factores ambientales.