Updated: February 2020
The harbour seal is a small phocid seal (“true seal”). They average around 150 cm in length and 70-100 kg in weight, and the males are generally larger than the females. Their coat colour pattern is very variable, but is usually silvery and darker on the back, creamy or lighter-grey on the belly and flanks, with dark spots covering the entire body. Pups can occasionally carry a fluffy white coat at birth, but this is usually shed in the uterus. This means that most of the time, pups are born in their adult-pattern coat (Bjørge et al. 2010).
Harbour seals are generalist predators, but prefer small to medium-sized fish. They are a coastal species that can be found hauling out in groups of up to several hundred animals.
There are estimated to be approximately 200,000 harbour seals in the North Atlantic.
They inhabit temperate to sub-Arctic waters along the eastern and western coasts of the North Atlantic. Svalbard is home to the northernmost population of harbour seals.
Harbour seals are hunted in Norway and Iceland for their meat and skin.
Scientific advice for the management of harbour seals in the North Atlantic is provided by NAMMCO. Management is the responsibility of each country.
In the most recent assessment (2016), the species is listed as being of ‘Least Concern’ on the European and global IUCN Red List, as well as on the Norwegian national red list. However, it is listed as ‘Vulnerable’ for Svalbard (Norway) and as ‘Critically Endangered’ on the Icelandic national red list.
Scientific name: Phoca vitulina
Danish: Spættet sæl/Spraglet sæl
English: Harbour seal, common seal
Females: 30-35 years, Males: 20-25 years
One pup per year
Generalist predator, with an overall preference for small to medium sized fish including cod, herring, sandeel, and flatfish
Around 150 cm in length and 70-100 kg in weight, with the males generally being larger than the females
The harbour seal (Phoca vitulina) is a coastal, non-migratory species. It can be found in the temperate and subarctic waters of the northern hemisphere. Four (marine) subspecies are recognised:
Eastern North Atlantic (P. v. vitulina; Linnaeus 1758) – distributed throughout Svalbard, Norway, Russia, Iceland, Denmark, Sweden, Germany, Poland, United Kingdom, Ireland, Netherlands, Belgium, France.
Western North Atlantic (P.v. concolor; DeKay 1842) – distributed from Labrador in Canada to Virginia in USA and in Greenland.
Eastern North Pacific (P. v.richardii; Gray 1864) – distributed throughout Alaska, some Russian islands, and the west coasts of Canada and the USA.
Western North Pacific (P.v. stejnegeri; Allen 1902) – distributed from eastern Siberia in Russia to northern Japan. This subspecies is also sometimes treated as a separate species, Phoca kurilensis or Phoca insularis (Bjørge et al. 2010).
Only the first two of these subspecies are found in the NAMMCO area.
There are, in addition, some landlocked harbour seals in lakes and connecting rivers in the Ungava Peninsula, Northern Quebec, Canada (Smith et al. 1996). These seals are recognized as a fifth (non-marine) sub-species: the Ungava seal P.v. mellonae (Doutt 1942).
Harbour seals are small phocid seals. They average around 150 cm in length and 70-100 kg in weight, and the males are generally larger than the females. The colour pattern of their coat is very variable, but usually silvery and darker on the back, creamy or lighter-grey on the belly and flanks, and with dark spots covering the entire body. Pups can occasionally carry a fluffy white coat (called lanugo) at birth, but this is usually shed in the uterus. This means that most of the time, pups are born in their adult-pattern coat (Bjørge et al. 2010).
Harbour seals show strong site fidelity. They move between haul-out sites and feeding areas, but rarely show seasonal migration. These seals haul out, give birth and nurse their young on beaches, sandbanks and rocks, usually in the intertidal zone along the coast. They also forage in close proximity to the coast. They can dive deeper than 200 m, but perform on average much shallower dives (60-100 m), mainly as a consequence of their habitat choice (Sharples et al. 2012, Ramasco 2015). The occurrence of resting dives, similar to the typical drift dives performed by other phocid seals (Crocker et al. 1997), has also been documented in harbour seals (Ramasco et al. 2013).
Harbour seals are opportunistic feeders, however they are more benthic (bottom of the sea) than pelagic (in the water column) feeders. They use different underwater feeding techniques, depending on prey type, including ambush, active search or digging with final pursuit (Bowen et al. 2002). They are highly social animals. Although they mostly feed independently, they gather to rest at haul out sites on a regular basis, usually timed with low tide in areas where the tidal cycle strongly impacts the geography of their habitat (Cronin et al. 2009).
Life History and Ecology
The annual reproductive cycle of most seal species is characterized by a tight synchrony of births, ensuring that pups are born at the optimal time of year (Boyd 1991). Across their range, harbour seals give birth to one pup per year between February and July, depending on the environmental conditions and population status, with lower latitudes and populations in good conditions breeding earlier (Reijnders, Brasseur, & Meesters 2010). Lactation lasts about three to four weeks, but the pup is able to swim already just a few minutes after birth. Male harbour seals come into breeding areas towards the end of the lactation time and perform underwater displays to attract females to mate (Van Parijs et al. 1997). Although harbour seals mate during this period, the females have delayed implantation. Harbour seal pregnancies last around eight months.
Harbour seals are known to be generalist predators, with an overall preference for small to medium sized fish (Ramasco 2015). They commonly feed on codfish (Gadidae), sandeel (Ammodytes sp.), herring (Clupea harengus) and flatfish (Pleuronectidae) depending on their surrounding habitat (Härkönen 1987, Olsen & Bjørge 1995, Bowen & Harrison 1996, Tollit et al. 1998). Differences in their diet (with seasonal and interannual variability) are documented across their geographical range (Härkönen 1987, Pierce et al. 1991, Hall et al. 1998). The shifts in diet over time are often linked to changes in the most abundant prey species to be found in their preferred size group (Ramasco, 2017). Harbour seals have been observed to respond to different prey pulses, such as seasonal increased concentration of herring or salmon (Middlemas et al. 2006, Thomas et al. 2011).
Distribution and Habitat
Harbour seals are distributed across temperate to sub-Arctic waters along the eastern and western coasts of the North Atlantic and the North Pacific Oceans (Bjørge et al. 2010). They primarily use areas close to the coastline, i.e. within 50 km (Jones et al. 2015), and generally do not perform seasonal migrations. In certain areas, for example where ice cover limits food or habitat accessibility during part of the year, the species shows small-scale seasonal migrations (Lesage et al. 2004).
North Atlantic stocks
Andersen & Olsen (2010) reviewed genetic studies done on harbour seal populations in the North Atlantic and identified twelve distinct populations: USA/Canada, Iceland, west coast of Norway, Ireland-Scotland, English east coast, Channel area, Wadden Sea, Limfjord, Skagerrak, Kattegat, West Baltic, and East Baltic/Baltic proper.
A subsequent study compared the Greenland and Svalbard populations to those that were geographically closest – mainland Norway and Iceland – and found them to be distinct (Andersen et al. 2011). Most of the genetic studies reviewed do not investigate potential population differences within each country, suggesting that the number of genetically distinct harbour seal populations is likely higher than 14. Two subsamples from Iceland that were analysed by Andersen et al. (2011) did not show significant differentiation though.
Current management units for Norwegian harbour seals are defined by county limits. However, information on the movement patterns of harbour seals in Norway (Bjørge et al. 2002b; Ramasco 2015) as well as recent genetic evidence of fine scale population structure in Danish and Swedish waters (Olsen et al. 2014), raises concerns that there may be population subdivisions within counties. Since some counties are quite large (with long coastlines), the management units are likely larger than the biologically significant populations.
Current Abundance and Trends
An estimate of the world population of harbour seals put them at approximately 610,000 – 640,000 individuals, including both the Atlantic and Pacific stocks (Bjørge et al. 2010). In 2016, the NAMMCO Scientific Committee endorsed the following table with abundance estimates from the Coastal Seals Working Group (NAMMCO 2016). A new meeting of the working group will take place in 2020 and it is expected that new information will be available following that meeting.
The NAMMCO Council has previously requested an assessment of the species in the North Atlantic. As a result, the Scientific Committee convened a Working Group to review the status of harbour seals throughout the North Atlantic, which resulted in Volume 8 of the NAMMCO Scientific Publications series being published in 2010 with a focus on harbour seals in the North Atlantic and Baltic. The working group met again in 2016 and noted that harbour seals appear to be declining in many areas (especially where grey seals are increasing), although there are little data to indicate if grey seals could have an impact on the harbour seal populations.
Harbour seals in Norway suffered a severe decline prior to the 1960s due to unregulated hunting (Øynes 1964). Regulatory measurements were introduced in 1973 in part of the country. A new management regime was implemented in 1997 with the aim to secure viable stocks. The most recent survey period (2011-2015) revealed a minimum total population of 7,642 harbour seals along the mainland Norwegian coast. This last estimate is close to the counts of 6,938 animals in 2003-2006 and 7,465 in 1996-1999, revealing a stable population trend since the 1990s (NAMMCO 2016).
A distinct population of around 1000 individuals is to be found in Svalbard (Lydersen & Kovacs 2010).
The Icelandic harbour seal population was considerably larger in the early 19th century than at present, with about 60,000 (90% CI = 40 – 100) animals. Aerial surveys conducted since 1980 indicate that the population has declined from 33,000 (90% CI = 26,000 – 44,000) animals in 1980 to about 12,000 (90% CI = 9,000 – 16,000) animals in 2006. Since 2003, total removals have decreased and the population decline appears to have ceased (Hauksson & Einarsson 2010). During the latest full census in 2016, the population was estimated to be about 7,700 animals (Þorbjörnsson et al. 2017), which is a decrease of 30% since 2011. The reasons for the decline are not known, but could include hunting, changes in prey species, by-catch (seals caught in fishing nets), ecosystem changes related to climate change, and disturbance from tourism. These issues are currently being investigated by researchers at the Marine and Freshwater Institute in Iceland, and the Icelandic Seal Center.
Southern Scandinavia (Kattegat, Skagerrak, Western Baltic, Limfjord)
The harbour seal population in Southern Scandinavia has experienced repeated declines caused by hunting and epizootics. Harbour seals have disappeared from haulout areas along the Danish shores of Kattegat and in the westernmost part of the Baltic Sea, where they were previously numerous. In the 1920-30s, when abundance was at its lowest, the population is estimated to have been only a fraction of its original size. Following 30 years of protection, the population is currently approaching historic abundance and seems to have reached the carrying capacity in some areas, showing a decrease in population growth rates, possibly caused by density dependent effects (Olsen et al. 2010).
The small population of harbour seals in the east Baltic (also called Baltic proper) was hunted close to extinction in the beginning of the 20th century and experienced a severe bottle-neck minimum numbers in the 1970s. Protective measures (in the form of a hunting ban and the establishment of protected areas) have improved the situation and the hauled-out moulting population size in 2008 was 588. Despite the conservation measures, however, the population in the east Baltic is not expected to reach favourable conservation status within the foreseeable future (Härkönen & Isakson 2010).
Mainland Europe (Wadden Sea)
The Wadden Sea harbour seal population has been severely depleted by hunting in the first half of the 20th century. After hunting was stopped in the mid-1970s, the population recovered gradually. This recovery was twice interrupted by PDV outbreaks in 1988 and 2002 (see below for further information). These epizootics reduced the population by 57% and 50% respectively. They also lead to changes in age and sex structure of the population, which gradually returned to stability (Reijnders, Brasseur, Tougaard, et al. 2010). After the outbreaks, the population showed a strong recovery with a growth rate close to the considered the maximum possible for this species, with a constant increase until 2013. Recent growth rates show that the overall increase of the population has slowed down, possibly suggesting it has reached carrying capacity (NAMMCO 2016).
The UK holds approximately 40% of the European harbour seal population, with the majority found around the coasts of Scotland (Thompson et al. 2010). A survey in 2011 counted 28,161 individuals in Great Britain, and 948 in Northern Ireland, for a total of 29,109 (NAMMCO 2016). A general decline has been observed in most harbour seal colonies around Scotland. The widespread declines, ranging from Shetland to the Wash, suggest that the causes, still unknown, may have been present over a large part of the North Sea and waters off western Scotland (Thompson et al. 2010). The populations in west Scotland and along the north, northwest and east coast of England appeared to have stable population numbers (NAMMCO 2016).
Faroe Islands and Greenland
The harbour seal was exterminated as a breeding species in the Faroe Islands in the mid-19th Century. For the last 40 years the harbour seal has only been positively identified twice in the Faroe Islands, in 2001 and 2005 (Mikkelsen 2010).
The total number of harbour seals in Greenland was estimated at about 3,000 in 1950 and fewer than 1,000 in 2007. The number of harbour seals in the southernmost part of Greenland has increased significantly in recent years, while historically used haulout locations along the west coast have gradually been abandoned after the 1950s (Rosing-Asvid 2010). Only four regularly used haulout places is presently known in Greenland. All hunting on this species was banned in 2010 and it is believed that several small remnant populations still exist, but live undetected.
A bounty harvest, as well as subsistence and commercial hunting, lead to a decline in the population from 1949 to the early 1970s. The bounty was removed in 1976 and harbour seals have been protected in the southern parts of their range since then. At that time, the total population south of Labrador was estimated to be 12,700 (Boulva and McClaren 1979). Since then, research has been limited to specific areas and there is little information available on total abundance and trends. For example, after increasing during the 1980s, harbour seal abundance on Sable Island underwent a rapid decline through the 1990s when it was estimated to be less than 100 animals (Bowen et al. 2003). In contrast, harbour seals are reported to have increased in the Bay of Fundy although the numbers are not known. There is some evidence suggesting that local abundance of seals at some known haulout sites in the more southern portions of Newfoundland and Labrador may have increased while abundance at sites in more northern areas of the west, northeast and Labrador coast are generally consistent with reports from the 1970s (Sjare et al. 2005). It has also been suggested that urban development resulting in habitat degradation is probably the most important factor affecting harbour seal populations in Atlantic Canada (Hammill et al. 2010).
Atlantic United States
The harbour seal is the most abundant and widespread seal species in this area. The number of harbour seals observed during the pupping season in this region has increased from about 10,500 animals in 1981 to 38,000 animals in 2001 (uncorrected counts, Waring et al. 2010). The corrected estimate of harbour seal abundance in 2001 was of 99,340 animals (CV=0.09) (Gilbert et al. 2005), this was higher than the most recent one in 2012, which was of 75,834 animals (CV=0.15, Waring et al. 2015a), indicating a slight decrease. Currently there is some uncertainty in the patterns of harbour seal abundance and distribution in the northeastern US. Johnston et al. (2015) document a decline in stranding and by-catch rates of harbour seals, providing support for an apparent decline in abundance.
Phocine Distemper Virus and fluctuations in abundance
Harbour seal abundances have fluctuated widely in the Northeast Atlantic in recent decades, mainly due to local outbreaks of the Phocine Distemper Virus (PDV). A first epidemic in 1988 killed about 50% of the harbour seals in Skagerrak-Kattegat, the Wadden Sea and the Wash in the UK, with the subsequent very rapid recovery of about 13% increase per year, and even higher growth rates observed regionally (Härkönen et al. 2006, Reijnders et al. 2010, Olsen et al. 2010). A new PDV epizootic struck the same populations in 2002 with mortality similar to (or in some areas less than) in 1988. A number of animals that gained immunity during the first epizootic may still have been part of the population in 2002 and thus contributed to there being less mortality.
In contrast to most other areas affected by the 2002 epizootic, the population in the Wash (UK) has continued to decline since the outbreak. A decline in harbour seal abundance since the late 1990s is also observed in Orkney, Shetland, and, to a lesser extent, in the Outer Hebrides and east Scotland. The abundance in west Scotland has, however, continued to increase (Thompson et al. 2010).
Other sources of mortality
Among the major sources of mortality are by-catch, predation by killer whales (Orcinus orca), competition, and viral outbreaks. The impact of predation by killer whales is unknown. In Norway, during winter, killer whales follow the over-wintering herring and may move closer to seal colonies and have been reported to eat harbour and grey seals. In Scotland, killer whale predation on harbour seals seems to be on the increase. Grey seals may also be a source of mortality for harbour seals, either as predators or as competitors. In various areas where harbour seals and grey seals overlap, the population growth rate of harbour seals is usually lower. This has been seen in the Baltic Sea, Sable Island (Canada), Scotland, and New England (US) (NAMMCO 2016).
The hunt in Norway has been regulated by quotas since 1997 and in 2003, the quotas and bounties were increased. After a decade with high quotas and a declining population of harbour seals, a management plan for harbour seals was implemented in 2010. There have been decreases in the yearly reported catches since 2011 when quotas began to be based on scientific advice.
Management units for Norwegian harbour seals are defined by county limits. However, there are concerns that there may be population subdivisions within counties. Harbour seals are regularly counted along the entire Norwegian coast at known haulout sites during the moulting period from mid-August to early September. The government has decided that the harbour seal population should be stabilized at a level where 7,000 moulting seals can be recorded. A balance between the preservation of large seal populations and reduced damage on fisheries and aquaculture in the coastal zone is desired.
In Iceland, seal hunting does not require a specific hunting license (only the license to own a weapon) and no specific quota system has been established for the seal populations. Seal hunting from land and shallow waters is managed by land owners and there are no special protected areas or protected periods (e.g., breeding season) of the year for seals except those imposed by land owners and general regulations on hunting. It is not mandatory to report direct seal catches to the government, however. reporting on by-catch is requried. Members of the Seal Farmers Union (SFU) can voluntarily report their catch statistics to the organization and other known hunters are contacted directly by the Icelandic Seal Center.
In 2006, the Icelandic government published a management plan where a minimum population size of 12,000 harbour seals was recommended (NAMMCO 2006). This recommendation has not been based on a biological assessment (NAMMCO 2016). The management plan states that management actions should be initiated if the population drops appreciably below that number, but no specific population regulating method has been mentioned.
Under the Conservation of Seals Act 1970, the UK Natural Environment Research Council (NERC) has a duty to provide scientific advice to the government on matters related to the management of seal populations. NERC has appointed a Special Committee on Seals (SCOS) to formulate this advice. Formal advice is given annually based on the latest scientific information provided to SCOS by the Sea Mammal Research Unit (SCOS 2004).
Harbour seals are regularly monitored through aerial surveys of animals hauled out during the annual moult in early August. The Scottish and English east coast populations mainly haul out in tidal estuaries and are surveyed annually, using fixed wing aircraft and digital photography. Populations in north and west Scotland often haul out on rocky shores and are surveyed less frequently, using helicopters fitted with thermal imagers (Thompson et al. 2010).
The department of Fisheries and Oceans Canada has published an Integrated Fisheries Management Plan for Atlantic Seals for the period 2011-2015 (see Grey seals). In this plan, hunting is regulated for most of the Atlantic seals in Canadian waters. Commercial harvesting for harbour seals is not permitted under this management plan.
Hunting and Utilisation
Despite their widespread presence, harbour seals are currently only hunted in Norway, Iceland and Atlantic Canada.
In Norway, hunting of harbour seals is a regulated recreational hunt. Ideally, seals are shot when they are hauled out. If seals are shot in the water, they need to be retrieved or they will otherwise sink and be lost. Hence, this hunt often occurs in shallow waters or with the use of a small vessel as support. The use of rifles with expanding bullets is mandatory.
Seal hunting in Iceland is focused almost entirely on seal pups, mainly for the skin; but the meat, the blubber (fat) and the flippers have played an important role for human consumption in the past. Pups are taken when they are a few weeks old, just towards the end of lactation. Net hunting around the river mouths is the most common method of hunting harbour seal pups. The hunting takes place in the spring. Annual takes range from 200 – 400 harbour seal pups. Harvests have declined in recent years because of the low market price of the skins. For a very long time before 1980, the catch was 4000 – 6000 harbour seal pups.
Greenland and Canada
In Greenland, all hunting of this species was banned in 2010.
In Nunavut (Atlantic Canada) harbour seals are hunted by Inuk people. There are currently no restrictions on the seasons or numbers of seals that can be harvested (Report of the Committee on Hunting Methods 2016).
Reported catches in NAMMCO member countries
This database of reported catches is searchable, meaning you can filter the information by for instance country, species or area. It is also possible to sort it by the different columns, in ascending or descending order, by clicking the column you want to sort by and the associated arrows for the order. By default, 30 entries are shown, but this can be changed in the drop-down menu, where you can decide to show up to 100 entries per page.
Carry-over from previous years are included in the quota numbers, where applicable.
You can find the full catch database with all species here.
You can find a complete file with all comments and explanations here, under Overview Documents.
For any questions regarding the catch database, please contact the Secretariat at email@example.com.
Other Human Impacts
By-catch and entanglements
By-catch of harbour seals during fishing operations and removals near fish farms are the major factors negatively impacting populations of this species in the North Atlantic.
In Norway, a coastal reference fleet (CRF) for the coastal gillnet fishery for cod and monkfish reports by-catch data and landings. Fisheries of concern are assumed to only be the gillnet fishery for cod and monkfish, with the primary species of concern being harbour and grey seals, as well as harbour porpoises. The estimated annual by-catch of harbour seals for the period 1997-2014 was on average 555 harbour seals. There is a peak of by-catch in the cod fishery in February-April, while the highest levels seen in the monkfish fishery occur from July-December.
In Iceland, the most reliable by-catch data originate from the March-April cod gillnet research survey and fisheries observers (1% coverage of the fleet and representative geographical spreading). The fisheries of most concern are assumed to be the gillnet fishery for cod and lumpsucker (NAMMCO 2016).
In US waters, the total human caused mortality and serious injury to harbour seals for the period 2008-2012 was estimated to be caused by US commercial fisheries on 97 % of the cases (Waring et al. 2015b).
Conflicts with fisheries & aquaculture
In Iceland and Norway, fish farmers have been allowed to remove seals near the farms by shooting them. In 2019, however, national regulations on coastal seals in Norway were amended and it is now prohibited to kill seals near aquaculture facilities. Interactions between seals and fish farms in Iceland are reduced by the use of double-netting. However, there are still some interactions between harbour seals and salmon fisheries around the river mouths, but removals are thought to be low, about 2-3 per year.
Commercial ship and vessel-based tourism are anthropogenic sources of disturbance for harbour seal colonies, causing potential shifts in local distribution and population decline (Jansen et al. 2015). Similar consequences can be due to habitat degradation caused by increased urbanization (Reijnders 1994).
In the UK between 2008 and 2010, several harbour seals were found stranded with peculiar injuries consisting of a single continuous curvilinear skin laceration spiralling down the body. Similar injuries were previously also observed in Canadian waters. After some investigation, the cause of death was found to be a traumatic event, with the seal being drawn through the ducted propellers of marine vessels (Bexton et al. 2012).
Pollutants are well known to negatively impact marine mammals. The levels of pollutants in harbour seals are generally regarded as low and do not constitute a health threat (Drescher et al. 1977). However, some environmental contaminants (especially persistent organic pollutants and mercury) are known to affect the immune system and might play a role in rendering marine mammal populations vulnerable to disease through immunotoxicity (Mos et al. 2006).
Research on harbour seals in Norway includes regular counts for abundance along the entire coast of Norway, but also studies on diet, behaviour, and the harbour seal’s role in the ecosystem. Since 2016, electric helicopter drones with cameras have been used in these surveys.
A recent study by scientists at the Institute of Marine Research on harbour seals in Porsangerfjord investigated diving, movements, and diet (Ramasco 2016). This study identified that harbour seals perform “resting dives”, which is a behaviour that has not been seen previously in this species. Harbour seals were also found to mainly forage during the day in the autumn and spring in Porsangerfjord. When comparing the seals’ diving behaviour to the presence of certain possible prey in the area, it is likely that seals are preferring small fish close to where the seals haul out. Their diet likely also changes with the seasons as different prey become available and when the sea ice forms.
Publications of results from genetic and population studies of harbour seals is currently also in progress (National Progress Report Norway 2018).
Research in Iceland hasin the last few years focused on getting updated abundance estimates and information on diet and prey selection, as well as information on movements and foraging behaviour in estuaries. Recently, results of a project looking at seal diets in river mouths in the northwest of Iceland was published (Granquist et al. 2018). A master’s project on vocalisations and behaviour of male Icelandic harbour seals during the mating season was also recently finished (National Progress Report Iceland 2018).
A survey of harbour seals was conducted in 2016 and indicated that the population was declining. The potential causes of the decline are not known. It is possible that hunting and by-catch (seals being caught in fishing nets) could be contributing to the decline, but the numbers of hunted and by-caught seals is not well known. Other factors that could be affecting harbour seals are the changes being seen in the ecosystem around Iceland, such as the warming of the water, and the associated northward movement of an important prey species such as the sandeel.
Another potential factor in the decline of harbour seals is disturbance from tourism, and studies by Burns et al. (2018) and Aquino et al. (2018) both look into the ethics of the tourism industry. These factors, and potentially the combination of all of them, are being investigated further by researchers in Iceland at the Marine and Freshwater Institute and the Icelandic Seal Center. Additionally, the NAMMCO By-Catch Working Group is working towards obtaining reliable estimates of seal by-catch.
The latest harbour seal aerial survey was conducted by the MFRI and ISC during 2018 and the analyses are still ongoing. The next aerial census is planned for 2020. A new project was initiated in 2018, monitoring haul-out behaviour using camera traps. This project will assist in improving census design by increasing the knowledge of factors affecting haul-out behaviour (National Progress Report Iceland 2018).
Harbour seals are rare in Greenland. The three known breeding/molting localities only hold around 100 seals, but observations of harbor seals far from these areas indicate that there are some additional small groups of seals with breeding and molting sites not yet detected. Current research aims to monitor the known sites and to locate the suspected additional sites. One of the three known sites was first registered in 2012 (after having been found by a hunter a few years earlier).
Andersen LW, Lydersen C, Frie AK, Rosing-Asvid A, Hauksson E, Kovacs KM (2011) A population on the edge: genetic diversity and population structure of the world’s northernmost harbour seals (Phoca vitulina). Biol J Linn Soc 102:420–439
Andersen L, Olsen MT (2010) Distribution and population structure of North Atlantic harbour seals (Phoca vitulina). In: Desportes G, Bjørge A, Rosing-Asvid A, Warning GT (eds) NAMMCO Scientific Publications. p.15
Aquino JF, Burns GL and Granquist SM (2018) Seal Watching in Iceland: Ethical Management Development. In J. Dehex (Ed.), The 9th International Conference on Monitoring and Management of Visitors in Recreational and Protected Areas (MMV9): Place, Recreation, and Local Development (pp. 165–167). Bordeaux, France. Retrieved from https://mmv9.sciencesconf.org/data/pages/last_version_abstract_book_7.pdf
Bexton S, Thompson D, Brownlow A, Barley J, Milne R, Bidewell C (2012) Unusual Mortality of Pinnipeds in the United Kingdom Associated with Helical (Corkscrew) Injuries of Anthropogenic Origin. Aquat Mamm 38:229–240
Bjørge A, Desportes G, Waring GT, Rosing-Asvid A (2010) Introduction: The harbour seal (Phoca vitulina) – a global perspective. In: Desportes G, Bjørge A, Rosing-Asvid A, Warning GT (eds) NAMMCO Scientific Publications. p 7
Bowen WD, Harrison GD (1996) Comparison of harbour seal diets in two inshore habitats of Atlantic Canada. Can J Zool 74:125–135
Bowen WD, Tully D, Boness DJ, Bulheier BM, and Marshall GJ (2002) Prey-dependent foraging tactics and prey profitability in a marine mammal. Mar Ecol Prog Ser 244:235–245
Bowen WD, McMillan J, and Mohn R. (2003) Sustained exponential population growth of grey seals at Sable Island, Nova Scotia. ICES J Mar Sci 60:1265-1274
Boyd IL (1991) Environmental and physiological factors controlling the reproductive cycles of pinnipeds. Can J Zool 69:1135–1148
Boulva, J., AND I. A. McClaren. 1979. Biology of the harbor seal, Phoca vitulina, in eastern Canada. Bull. Fish. Res. Board Can. 200: 24 p.
Burns GL, Öqvist EL, Angerbjörn A and Granquist S (2018) When the wildlife you watch becomes the food you eat: Exploring moral and ethical dilemmas when consumptive and non-consumptive tourism merge. In Kline, C (ed), Animals, food, and tourism pp. 22-35. Routledge Ethics of tourism: New York.
Crocker DE, LeBoeuf BJ, Costa DP (1997) Drift diving in female northern elephant seals: implications for food processing. Can J Zool 75:27–39
Cronin M (2010) A modelling framework to optimize timing of haulout counts for estimating harbour seal (Phoca vitulina) abundance. In: Desportes G, Bjørge A, Rosing-Asvid A, Waring GT (eds) Harbour seals in the North Atlantic and the Baltic. NAMMCO Scientific Publications, Volume 8, Tromsø, p 213–226
Cronin M, Zuur A, Rogan E, McConnell B (2009) Using mobile phone telemetry to investigate the haul-out behaviour of harbour seals Phoca vitulina vitulina. Endanger Species Res 10:255–267
(CSWG) Report of the Coastal Seals Working Group (2016) Reykjavik, Iceland. Available at: https://nammco.no/topics/sc-working-group-reports/
Drescher HE, Harms U, Huschenbeth E (1977) Organochlorines and heavy metals in the harbour seal Phoca vitulina from the German North Sea Coast. Mar Biol 41:99–106
Gilbert JR, GT Waring, KM Wynne, and N Guldager. 2005. Changes in abundance of harbor seals in Maine, 1981–2001. Marine Mammal Science, 21: 519–535.
Granquist SM, Hauksson E (2016) Seasonal, meteorological, tidal and diurnal effects on haul-out patterns of harbour seals (Phoca vitulina) in Iceland. Polar Biol 39:2347–2359
Granquist, SM, Hauksson, E, Árnadóttir, A, and Kasper, J 2011. Landselstalning úr lofti árið 2011. Framvinda og niðurstöður [Aerial survey of the Icelandic harbour seal population]. Institute of Freshwater Fisheries, November 2011. VMST/11051
Granquist SM, Esparza-Salas R, Hauksson E, Karlsson O and Angerbjörn A (2018) Fish consumption of harbour seals (Phoca vitulina) in north western Iceland assessed by DNA metabarcoding and morphological analysis, Polar Biology, 1-12.
Hall AJ, Watkins J, Hammond PS (1998) Seasonal variation in the diet of harbour seals in the south-western North Sea. Mar Ecol Prog Ser 170:269–281
Hammill MO, Bowen WD, Sjare B (2010) Status of harbour seals (Phoca vitulina) in Atlantic Canada. NAMMCO Sci Publ 8:175
Hauksson E, Einarsson ST (2010) Historical trend in harbour seal (Phoca vitulina) abundance in Iceland back to the year 1912. NAMMCO Sci Publ 8:147
Härkönen T (1987) Seasonal and regional variations in the feeding -habits of the harbor seal, Phoca vitulina, in the Skagerrak and the Kattegat. J Zool 213:535–543
Härkönen L, Dietz R, Reijnders PJH, Teilmann J, Harding K, Hall A, Brasseur SMJM, Siebert U, Goodman SJ, Jepson PD, Rasmussen TD, Thompson P (2006) A review of the 1988 and 2002 phocine distemper virus epidemics in European harbour seals. Dis Aquat Organ 68:115–130
Härkönen T, Isakson E (2010) Status of harbour seals (Phoca vitulina) in the Baltic proper. NAMMCO Sci Publ 8:71
Jansen JK, Boveng PL, Hoef JM Ver, Dahle SP, Bengtson JL (2015) Natural and human effects on harbor seal abundance and spatial distribution in an Alaskan glacial fjord. Mar Mammal Sci 31:66–89
Johnston DW, J Frungillo, A Smith, K Moore, B Sharp, J Schuh, and AJ Read. 2015. Trends in stranding and by-catch rates of gray and harbor seals along the Northeastern coast of the United States: Evidence of divergence in the abundance of two sympatric phocid species? PLoS ONE 10(7): e0131660. doi:10.1371/journal.pone.0131660
Jones EL, McConnell BJ, Smout S, Hammond PS, Duck CD, Morris CD, Thompson D, Russell DJF, Vincent C, Cronin M, Sharples RJ, Matthiopoulos J (2015) Patterns of space use in sympatric marine colonial predators reveal scales of spatial partitioning. Mar Ecol Prog Ser 534:235–249
Lesage V, Hammill MO, Kovacs KM (2004) Long-distance movements of harbour seals (Phoca vitulina) from a seasonally ice-covered area, the St. Lawrence River estuary, Canada. Can J Zool 82:1070–1081
Lydersen C, Kovacs KM (2010) Status and biology of harbour seals (Phoca vitulina) in Svalbard. NAMMCO Sci Publ 8:47
Middlemas SJ, Barton TR, Armstrong JD, Thompson PM (2006) Functional and aggregative responses of harbour seals to changes in salmonid abundance. Proc R Soc B Biol Sci 273:193–8
Mikkelsen B (2010) A note on the harbour seal (Phoca vitulina) in the Faroe Islands. NAMMCO Sci Publ 8:143
Mos L, Morsey B, Jeffries SJ, Yunker MB, Raverty S, Guise S De, Ross PS (2006) Chemical and biological pollution contribute to the immunological profiles of free-ranging harbor seals. Environ Toxicol Chem 25:3110
(NAMMCO) North Atlantic Marine Mammal Commission. (2016) Report of the Coastal Seals Working Group. Reykjavik, Iceland. Available at http://nammco.wpengine.com/wp-content/uploads/2016/09/report-of-the-cswg-march-2016.pdf
Olsen MT, Andersen SM, Teilmann J, Dietz R, Edrén SMC, Linnet A, Härkönen T (2010) Status of the harbour seal (Phoca vitulina) in Southern Scandinavia. NAMMCO Sci Publ 8:77
Olsen M, Bjørge A (1995) Seasonal and regional variations in the diet of harbour seal in Norwegian waters. In: Blix AS, Walloe L, Ulltang Ø (eds) Whales, seals, fish and man. Elsevier, Amsterdam, p 271–285
Parijs SM Van, Thompson PM, Tollit DJ, Mackay A (1997) Distribution and activity of male harbour seals during the mating season. Anim Behav 54:35–43
Pierce GJ, Thompson PM, Miller A, Diack JSW, Miller D, Boyle PR (1991) Seasonal-variation in the diet of common seals (Phoca-vitulina) in the Moray-Firth area of Scotland. J Zool 223:641–652
Ramasco V (2017) Selection and foraging response of harbour seals in an area of changing resources. Mar Ecol Prog Ser 581: 199-214.
Ramasco V (2015) Spatial and temporal patterns of foraging of harbour seals (Phoca vitulina) in Porsangerfjord, from behavioural interpretation to resource selection. UiT, the Arctic University of Norway
Ramasco V, Barraquand F, Nilssen KT, Mcconnell B (2013) Identifying periods of “resting” at sea helps making sense of harbour seals’ foraging signature in movement data. In: Proceeding of the 20th Biennial Conference on the Biology of Marine Mammals. Dunedin (NZ)
Reijnders PJH (1994) Historical population size of the harbour seal, Phoca vitulina, in the Delta area, SW Netherlands. In: The Oosterschelde Estuary (The Netherlands): a Case-Study of a Changing Ecosystem. Springer Netherlands, Dordrecht, p 557–560
Reijnders PJH, Brasseur SMJM, Meesters EHWG (2010) Earlier pupping in harbour seals, Phoca vitulina. Biol Lett 6
Reijnders PJ, Brasseur SM, Tougaard S, Seibert U, Borchardt T, Stede M (2010) Population development and status of harbour seals (Phoca vitulina) in the Wadden Sea. NAMMCO Sci Publ 8:95
Report of the Committee on Hunting Methods (2016) Oslo, Norway
Rosving-Asvid A (2010) Catch history and status of the harbour seal (Phoca vitulina) in Greenland. NAMMCO Sci Publ 8:161
Sjare B, Lebeuf M, and Veinott G. (2005) Harbour seals in Newfoundland and Labrador: a preliminary summary of new data on aspects of biology, ecology and contaminant profiles. DFO Can. Sci. Advis. Sec. Res. Doc. 2005/030.
[SCOS] Special Committee on seals. Scientific advice on matter related to the management of seal populations: 2004 (2004). Available from http://www.smru.st-andrews.ac.uk/research-policy/scos/
Sharples RJ, Moss SE, Patterson T a, Hammond PS (2012) Spatial variation in foraging behaviour of a marine top predator (Phoca vitulina) determined by a large-scale satellite tagging program. PLoS One 7:e37216
Smith RJ, Hobson KA, Koopman HN, Lavigne DM (1996) Distinguishing between populations of fresh- and salt-water harbour seals (Phoca vitulina) using stable-isotope ratios and fatty acid profiles. Can J Fish Aquat Sci 53:272–279
Thomas A, Lance M, Jeffries S, Miner B, Acevedo-Gutiérrez A (2011) Harbor seal foraging response to a seasonal resource pulse, spawning Pacific herring. Mar Ecol Prog Ser 441:225–239
Thompson D, Duck C, Lonergan ME (2010) The status of harbour seals (Phoca vitulina) in the United Kingdom. NAMMCO Sci Publ 8:117
Tollit DJ, Black AD, Thompson PM, Mackay A, Corpe HM, Wilson B, Parijs SM Van, Grellier K, Parlane S (1998) Variations in harbour seal Phoca vitulina diet and dive-depths in relation to foraging habitat. J Zool 244:209–222
Waring, GT, RA DiGiovanni Jr, E Josephson, S Wood, and JR Gilbert. 2015a. 2012 Population estimate for the harbor seal (Phoca vitulina concolor) in New England waters. US Dep. Of Commer., NOAA Technical Memorandum NMFS-NE-235, 15p.
Waring GT, Gilbert JR, Belden D, Atten A Van, DiGiovanni Jr RA (2010) A review of the status of harbour seals (Phoca vitulina) in the Northeast United States of America. NAMMCO Sci Publ 8:191
Waring GT, E Josephson, K Maze-Foley, PE Rosel, editors. 2015b. US Atlantic and Gulf of Mexico Marine Mammal Stock Assessments — 2014. NOAA Tech Memo NMFS NE 231; 361 p. doi: 10.7289/V5TQ5ZH0
Wilson LJ (2014) The diet and feeding ecology of harbour seals around Britain. University of St. Andrews
Øynes P (1964) Sel på norskekysten fra Finnmark til Møre. Fisk Gang 50:694–707