Epinephelus rankini was previously a synonym of this species (Cao et al. 2022).

This widely distributed species inhabits reefs and can be locally abundant in parts of its range. It is harvested in many areas, and landings, while fluctuating, show a modest downward trend (e.g. the Seychelles, Saudi Arabia, Kuwait, Reunion and Rodrigues Island). An overall global population decline approaching 30% over the past three generation lengths (~48 years) is not suspected at this time; therefore, it is listed as Least Concern. It is strongly recommended that heavily exploited subpopulations be closely monitored and fisheries management improved. Further research on its reproductive biology and life history would also be beneficial.

This species is distributed in the Indian Ocean from the Persian Gulf and Gulf of Oman south along the coastline of East Africa to southern Mozambique, including the islands of the Western Indian Ocean, and east to the Maldives and the Chagos Archipelago (Cao et al. 2022). It has also been recorded in western India (R. Nair pers. comm. 2023) and northeast South Africa (Chater et al. 1993, S. Fennessy pers. comm. 2023). Records from Western Australia and southeastern Indonesia are now attributed to Epinephelus rankini (Cao et al. 2022). The depth range is 1-90 m (Cao et al. 2022).

This is considered to be a common species throughout its range (Craig et al. 2011), though it can be relatively uncommon in some areas. It has at least two geographically separated sub-populations based on differences in colour pattern and scale counts: 1. Western Indian Ocean; 2. Persian Gulf and Gulf of Oman. Species-specific population information is limited in some areas and some landings are unreported (Jacquet et al. 2010). There are some indications of declines in parts of its range due to overfishing, including in the Seychelles (declining catch rates up to 50%), Kuwait, Saudi Arabia (Persian Gulf), Reunion and Rodrigues Island, but overall, the population of this species is unlikely to have declined by more than 30% over its global range over the past three generation lengths, or about 48 years (Bunce et al. 2008, Pistorius and Taylor 2009, Al-Zaidan et al. 2013). 

Persian Gulf and Gulf of Oman: Species-specific landings were first reported to FAO by Saudi Arabia (Persian Gulf) in the early 2000s with 1,100 tonnes in 2001, and from 2002-2010 average landings were around 400 tonnes per year, increased in 2011 and 2012 to more than 1,000 tonnes and declined thereafter to 49 tonnes in 2014 (FAO 2016). This represents a 96% decline over a 13 year time period. In Kuwait, it is targeted by the artisanal fishery, where fishery production doubled between 1980 and mid-2000s and is expected to continue increasing (Al-Zaidan et al. 2013). In 2004-2005, Kuwait's local gargoor trap fishery landed 13.4 kg of Epinephelus multinotatus, which comprised 0.17% of the total catch by weight (Chen et al. 2012). Aggregate grouper landings reported from Kuwait, Qatar, and Bahrain over the past 24 years show no clear trend (FAO 2016). From 2004-2008, landings of this species in Bahrain were 0.5 metric tonnes in 2004 and 0.3 mt in 2008, and from 2009-2012, no landings of this species were recorded (E. Abdulqader pers. comm. 2013). From 1979-2012, landings of this species in Kuwait fluctuated, with 186 mt harvested in 1979 and 2,059 mt in 2012, with a peak of 5,355 mt in 1986 (J. Bishop pers. comm. 2013). Deeper-water groupers of large size are extensively fished in Oman and the Arabian Sea both by line fishing and trawling, and concerns have been raised that this assemblage is subject to high levels of fishing in Oman (J. McIlwain unpublished data). Aggregate fisheries catch statistics for groupers indicate a 43% decline over a range of 3-11 years and effort is likely to increase over the next 10-15 years in the region.

Western Indian Ocean: During shallow underwater surveys conducted from 2009-2015 in six countries (Tanzania, northern Mozambique, northeastern Madagascar, Comoros, Chagos and Isles Glorieuses) only one individual of this species was observed in Chagos. Additional surveys found two individuals – one in northern Kenya and one in northeastern Madagascar (M. Samoilys unpublished data). This suggests that this species is rare or does not typically occur on shallow reefs. It is possibly naturally uncommon in mainland East Africa as it was not observed in underwater surveys (to ~20 m depth) along the Kenyan coast in the past, or in southern Tanzania’s Mnazi Bay Ruvuma Estuary Marine Park (Obura et al. 2004), though this may be a reflection of its deeper depth preferences.

This species was relatively abundant in the Seychelles and was the most common of the three grouper species taken in demersal handline fisheries there (Mees 1992, MRAG 1996). Densities in shallow (less than 20 metres depth) in the Seychelles ranged from 0 to 0.51 fish/1,000 m², with higher densities found in the Amirantes Isles (Pears 2005). Its population in the Seychelles was overfished by at least 2007 (J. Robinson pers. comm. 2007). Fishing activity on spawning aggregations in the Seychelles can yield between 400 and 8,000 kg in a single fishing trip (Robinson et al. 2007). A 61% decline in catch per unit effort over a ten year period (1996-2007) was documented in Aldabra’s marine protected area (Seychelles) based on landings from a small subsistence fishery and the decline is thought to be caused mainly by reef degradation (Pistorius and Taylor 2009). In 2009, catch in the hook and line fishery of the Seychelles totaled 2.2 tonnes (WIOfish 2016). 

This species is one of the 19 grouper species taken in the small-scale artisanal fishery around Réunion and estimated total catches declined from about 20 to 45 mt from 1998 to 2002, and further to 3 mt in 2004-2005, and no effort data are available (D. Miossec pers. comm. 2007). According to fishermen in Rodrigues Island, this species reportedly declined by number and body size over the past 25 years (Bunce et al. 2008). Very limited deeper (30 m) fisheries occur in East Africa, though hook and line, seine, traps and trawl are listed for taking groupers in Tanzanian waters. Some illegal foreign fishing vessels trawling the shelf area beyond territorial waters may be taking this species (Samoilys 2004). It is reported from catches in 2000, 2002 and 2003 of the commercial hook and line fishery of Mozambique (S. Fennessy pers. comm. 2007). The relative abundance of this species in artisanal fisheries in southern Kenya was low (1-5% of grouper catch (Agembe et al. 2010). Landings are known to be unreported in some countries of East Africa (Jacquet et al. 2010).

This species inhabits coral and rocky reefs, including drop-offs and banks (Randall 1995, J. Robinson pers. comm. 2007). Juveniles can be more common on coral reefs, while adults are often found in deeper waters around sandy or rocky substrates (Carpenter et al. 1997, Cao et al. 2022). 

The maximum total length is 100 cm (Cao et al. 2022) and the maximum age is 30 years (Grandcourt 2005). Spawning aggregations of Epinephelus multinotatus are reported during peak reproductive months (Wheeler and Ommanney 1953, Robinson et al. 2004) and non-aggregating spawning likely occurs at other times during the year (J. Robinson pers. comm. 2007). In the Seychelles, spawning occurs year-round with a peak from August to October during which spawning aggregations may form (Robinson et al. 2007). Age at first maturity is not available for this species, but the related species E. rankini, which has an age at maturity of two years (Newman et al. 2021), is applied here as an appropriate proxy (M.T. Craig pers. comm. 2023). When applying an age at first reproduction of 2 years and longevity of 30 years, its estimated generation length is 16 years based on the following equation recommended by the IUCN Red List methods: age at first reproduction + (age at last reproduction – age at first reproduction)/2.

Overfishing is a threat to this species in parts of its range (Craig et al. 2011, Chabanet et al. 2016). Reef degradation may also negatively impact this species (Pistorius and Taylor 2009).

This species is taken in fisheries in much of its range. It is mainly caught using hook and line and traps and may also be a component of bycatch in trawl fisheries (Heemstra and Randall 1993). It is a primary commercial species in Kuwait's gargoor trap fishery (Chen et al. 2012). This was the sixth most important species out of seven in terms of exported quantities for the live reef food fish trade in the Seychelles, but this export has been banned since the early 2000s. It is an important species in Seychelles artisanal fisheries (Bodin et al. 2020). It has been sparsely recorded in fisheries catches off western India (R. Nair pers. comm. 2023).

Some fisheries management is in place in the Seychelles and regulations are reasonably well-enforced. The live reef food fish trade in the Seychelles was closed by the early 2000s due to sustainability concerns, conflicts with local fishers, biodiversity and economic viability (Aumeeruddy and Robinson 2006). This species receives some protection in extensive no-take protected areas on the east coast of South Africa, and also in MPAs in southern Mozambique, Chagos and Kenya (S. Fennessy pers. comm. 2023). 

Research is needed on its life history.