Abondance des oiseaux de mer
D1 - Diversité Biologique
D1.2 - Taille des populations
On considère que l’abondance des espèces d’oiseaux de mer évalués dans l’ensemble de la zone maritime OSPAR n’est pas indicatrice d’une bonne santé depuis le milieu des années 2000. Les espèces qui utilisent les zones intertidales et côtières de la mer du Nord au sens large au cours de leur migration ou durant leur hivernage font exception et leur nombre est appréciable depuis le début des années 1990.
Les oiseaux de mer dépendent de diverses sources de nourriture dans le milieu marin. Ils sont sensibles à diverses pressions, notamment la pêche, la prédation par des mammifères non-indigènes (par exemple, rats et vison d’Amérique), la perte d’habitat et les modifications de la qualité de l’eau.
On utilise l’abondance (nombre d’oiseaux ou de couples adultes dans les colonies de nidification) à titre d’indicateur car il est facile de la mesurer et d’évaluer les modifications à long terme de la structure des communautés et elle change lentement dans des conditions naturelles. Des modifications rapides des nombres peuvent indiquer des impacts anthropiques et, étayées par des valeurs d’évaluation propres aux espèces sur l’ampleur du déclin, elles peuvent déclencher des mesures de gestion. Des modifications historiques sont notamment le fait que de nombreuses espèces ont bénéficié des rejets de poisson par l’industrie de la pêche.
Dans le cas des oiseaux de mer, cette évaluation se fonde principalement sur les données portant sur « l’abondance des reproducteurs ». Dans le cas des oiseaux aquatiques (sauvagine et échassiers) cette évaluation se fonde principalement sur les données portant sur « l’abondance des non-reproducteurs » (nombres d’oiseaux utilisant les zones intertidales et côtières au cours de leur migration ou durant leur hivernage). Les estimations annuelles de l’abondance des reproducteurs et celles des non-reproducteurs sont comparées aux valeurs d’évaluation conçues pour refléter la résistance de diverses espèces au déclin des populations. II est souhaitable que l’abondance annuelle relative d’une espèce soit supérieure à 0,8 (80% de la ligne de base) pour les espèces qui pondent un œuf ou 0,7 (70% de la ligne de base) pour les espèces qui pondent plusieurs œufs. On considère qu’un ensemble d’espèces d’oiseau est sain si au moins 75% des espèces évaluées dépassent leurs valeurs d’évaluation individuelles.
This indicator includes information on marine bird species that, at some point in their annual life cycle, are reliant on coastal and / or offshore marine areas. The indicator is constructed from species-specific trends in annual abundance and includes:
- Breeding abundance: estimated from counts of adult birds or pairs on land at breeding colonies or sites, nesting close to the coast, and using the marine environment (e.g. for food); and
- Non-breeding abundance: estimated from counts of adult birds in intertidal areas or close to the shore and counted from land or from the air during migration or over the winter.
Abundance indicators could also be constructed from time series data collected at sea, but few data were available to be able to do so on this occasion.
In this context, marine birds include the following taxonomic groups that are commonly aggregated as waterbirds and seabirds:
- Waterbirds: shorebirds (Charadriiformes); ducks, geese and swans (Anseriformes); divers (Gaviiformes); and grebes (Podicipediformes); and
- Seabirds: petrels and shearwaters (Procellariiformes); gannets and cormorants (Suliformes); skuas, gulls, terns and auks (Charadriiformes).
Shorebirds, some duck species and some gulls feed on benthic invertebrates in soft intertidal sediments and on rocky shores. Geese graze on exposed eelgrass beds (Zostera spp.) as well as coastal marshes. Diving duck species feed on invertebrate benthos in shallow inshore waters. All other marine birds, including some gulls, spend the majority of their lives at sea, feeding on prey living within the water column (i.e. plankton, fish and squid) or picking detritus from the sea surface. Divers, piscivorous ducks, grebes, cormorants, gulls and terns tend to be confined to inshore waters, whereas petrels, shearwaters, gannets, skuas and auks venture further offshore and beyond the shelf break.
Most seabirds are assessed using breeding abundance, because they are easier to count when they aggregate on land to breed than when they are dispersed at sea over large areas. Most waterbirds are assessed using non-breeding abundance, because they are much easier to count when they are migrating or during the winter when they aggregate in intertidal and inshore areas. Waterbirds tend to be more difficult to count during the breeding season, because most species do not tend to breed colonially and nesting pairs are distributed over large areas. Many waterbird species in this assessment breed inland and in areas outside the OSPAR Maritime Area.
The assessment values used in this indicator assessment were developed for breeding seabirds’ abundance data in order to assess the OSPAR Ecological Quality Objective (EcoQO) on seabird population trends as an index of seabird community health (ICES, 2008, 2010, 2011, 2012). This indictor supersedes the EcoQO as it incorporates data on more species, including waterbirds and also uses data on non-breeding abundance. This indicator has gone through extensive testing and development (see ICES, 2013a,b,c,d, 2015). OSPAR IA2017 indicator assessment values are not to be considered as equivalent to proposed European Union Marine Strategy Framework Directive (MSFD) criteria threshold values, however they can be used for the purposes of their MSFD obligations by those Contracting Parties that wish to do so.
This indicator has relevance for two seabird species included in the OSPAR List of threatened and/or declining species and habitats (OSPAR Agreement 2008-6): black-legged kittiwake (Rissa tridactyla) and roseate tern (Sterna dougallii). It may also include the fuscus sub-species of lesser black-backed gull Larus fuscus fuscus, in the assessment of the Norwegian Sea and the Barents Sea. The OSPAR List was developed on the basis of the Texel-Faial criteria for identifying species and habitats in need of protection (OSPAR Agreement 2003-13). Assessments of abundance distribution and condition of the seabird species on the OSPAR List were prepared for the Quality Status Report 2010 and are included in its supporting documentation, but no comparable quantitative assessment was prepared.
This indicator assessment begins by constructing a time series of annual estimates of ‘relative breeding abundance’ or ‘relative non-breeding abundance’ of each species in each OSPAR Region or sub-division thereof (see section on Spatial Aggregation and Figure a). For the majority of species, data are available for breeding abundance or non-breeding abundance; both are available for only five species in the Arctic Waters, 14 species in the Greater North Sea and just one species in the Celtic Seas. Relative abundance is the number of adult birds or breeding pairs estimated each year as a proportion of a baseline (see section below on parameter/metric). Each species-specific estimate of annual relative abundance is compared against an assessment value. This indicator assessment is based on the proportion of species in a region or sub-division of that region that have exceeded assessment values for relative abundance in the most recent year of the time series. Separate assessments were carried out for relative breeding abundance and relative non-breeding abundance.
This indicator assessment is confined to three OSPAR Regions: Arctic Waters, the Greater North Sea and the Celtic Seas. The assessment of Arctic Waters is based on data from Norway only, but includes both breeding and non-breeding abundance data from both the Norwegian Sea and Barents Sea (excluding Jan Mayen and Svalbard). The assessment of the Greater North Sea includes both breeding and non-breeding abundance data from all Contracting Parties, except France. The assessment of the Celtic Seas is based on breeding abundance data from Ireland and the United Kingdom and on non-breeding abundance data from the United Kingdom only. No assessments were possible for the Bay of Biscay and Iberian Coast and for the Wider Atlantic because no data were provided to this assessment by France, Spain and Portugal.
Species-Specific Indicators of Relative Abundance
In 2016, the following data were requested from Contracting Parties on counts of breeding and non-breeding adult birds collected during the period 1980–2015:
- Breeding seabird colonies and breeding waterbirds nesting close to the coast and using the marine environment (e.g. for food): counts of breeding pairs (preferably, or failing that adult birds) per species per colony per year.
- Wintering and migrating waterbirds: numbers of birds per species per site per year that are counted from land or from the air. These data mostly comprise maximum or single counts conducted in January (N.B. within the Arctic Circle counts are conducted in March when there is sufficient daylight to do so). Data from the Wadden Sea Trilateral (Germany, Netherlands and Denmark) Monitoring and Assessment Programme and from the United Kingdom Wetland Bird Survey also comprised a mean of counts conducted throughout a one-year period (from July in one year to June in the next).
Most data refer to individual colonies or sites rather than large stretches of coastline. Exceptions are the Wadden Sea, the Dutch Delta and for non-breeding data in the United Kingdom, where colonies have been aggregated to regions and sub-divisions.
Separate indicator assessments were conducted for each species in each OSPAR Region. An assessment was also conducted for each sub-division of the Greater North Sea, and the mainland part of the Norwegian Arctic Waters (Figure a). These smaller sub-divisions may help to interpret the assessment results. The sub-divisional boundaries are based on a coarse assessment of the main oceanographic features such as currents and depth, and some relatively clear-cut differences in seabird / waterbird community structure and population trends (ICES, 2013c,d).
Data used in this Assessment
When all data from participating Contracting Parties had been collated, it became clear that prior to 1992, the number of annual counts per site was much lower in some areas, with many sites not being surveyed at all. Prior to 1992, a large amount of data would need to be interpolated and confidence in the accuracy of trends in abundance during this period would be very low. For this reason, the data used in this indicator assessment were restricted to 1992 onwards. The Arctic Waters and Celtic Seas regional scale assessments used data collected during the period 1992–2015. In the Greater North Sea, regional assessments were only possible for the period 1992–2014, because more recent data were not available for the Wadden Sea.
In the Wadden Sea (Denmark, Germany, Netherlands), the status of non-breeding waterbirds is best indicated by year-to-year change in the mean of counts conducted throughout the year (i.e. from July in one year to June in the next) (Blew et al., 2016). These year-round counts are also conducted in the United Kingdom and in the Netherlands (outside of the Wadden Sea), but are not carried out elsewhere in the Greater North Sea. All Contracting Parties supplied maximum or single counts conducted in January (N.B. within the Arctic Circle, counts are conducted in March when there is sufficient daylight to do so). The January counts were used for the indicator assessment in the Greater North Sea region as a whole and separately, in each Greater North Sea sub-division, apart from the southern North Sea (sub-division d in Figure a), where mean year-round counts from the United Kingdom, Netherlands, Germany and Denmark were used (year-round counts were not available for Belgium). Year-round counts for the Wadden Sea (Denmark, Germany, Netherlands) were only available up to July 2013- June 2014 (i.e. 2013/14). Hence, the indicator assessments for each of the Greater North Sea sub-divisions were restricted to the period 1992/93 – 2013/14.
This indicator assessment requires for each species an annual estimate of either breeding or non-breeding abundance (depending on species) per site or colony. Not all the colonies and sites in the data provided had been observed every year. Missing annual observations were interpolated from the observed data using statistical models. The minimum number of years of counts for a particular species required for a colony or site to be included in the analysis was set at two for all species except northern fulmar (Fulmarus glacialis), which was set at a minimum of five years (ICES, 2010, 2011).
Some Contracting Parties provided data that had no missing values because these had already been interpolated prior to submission, using tried and tested methods:
1. United Kingdom non-breeding abundance, all species (for methodology see Underhill et al., 1994).
2. Denmark, Germany and the Netherlands in the Wadden Sea (Greater North Sea sub-division d) non-breeding abundance, all species (for methodology see Blew and Südbeck, 2005; Blew et al., 2016; see also www.waddensea-infogate.org/Migratory%20Birds/Migratory_birds.html).
3. Denmark, Germany and the Netherlands in the Wadden Sea (Greater North Sea sub-division d) breeding abundance, all species (for methodology see Koffijberg et al., 2015; see also www.waddensea-infogate.org/Breeding%20Birds/Breeding_birds.html).
For all other data submitted by Contracting Parties, missing annual observations were interpolated using a modified chain method, first developed by Thomas (1993). This method estimates values of missing observations based on information in other years and sites. The advantage of this method is that it allows for site-specific variation, thereby avoiding the conventional assumption that changes in abundance at different sites occur synchronously. A further advantage of this approach is that it can easily incorporate counts of whole colonies and counts from smaller plots within the same colonies that are monitored more frequently than the whole colony. The Thomas estimation method has been used to construct trends in abundance for earlier iterations of this indicator and its OSPAR Ecological Quality Objective (EcoQO) predecessor. Details of the method are as reported by ICES (2008: Annex 3).
Applying Regional Weightings to Abundance Trends
Not all the colonies or sites in an assessment unit will be monitored and present in the dataset. The proportion of a population that is monitored varies between species and between countries. There is a resultant bias, in that those countries where few sites are monitored are under-represented in the trends for a given assessment unit, compared to those countries where a larger proportion of sites are monitored.
To remove such bias, the annual estimates of breeding and non-breeding abundance in each country were weighted according to the size of the population in that country. Each Contracting Party provided recent estimates of total abundance for each species along their coastline within each of the assessment units in Figure a. To apply a regional weighting, each annual estimate of abundance in each assessment unit was divided by a proportion p, where p is the proportion of the total population that is present within the sites or colonies that are included in the data provided. The total number of adult birds or pairs in an assessment unit were, in most instances, taken from national censuses.
As an example, the weighted annual breeding abundance of a species in the Celtic Seas region, yIII in year j, was calculated from annual estimates of abundance in each constituent country, i.e. the United Kingdom Celtic Seas coast (yUK) and Ireland (yIRE) as follows:
yIIIj = (yUKj / pUK) + (yIREj / pIRE)
where pUK and pIRE are the proportions of the respective populations in the United Kingdom (UK) and Ireland (IRE) that are contained in the sample of colonies that were monitored in each constituent country in the Celtic Seas region.
Regional weightings were not necessary where data contained all the colonies or sites in that area. In Belgium, all the breeding and non-breeding sites in the country are monitored, so no weightings were required for these data. Regional weighting was also not necessary for estimates of annual abundance that had been interpolated before submission. These included trends in breeding and non-breeding abundance in the Dutch, German and Danish Wadden Sea, and trends in non-breeding abundance in the United Kingdom.
To compare the state of species that have very different population sizes, estimates of abundance (measured in numbers of adult birds or breeding pairs) were converted to an indicator metric that uses a single scale (i.e. a proportion) for all species. The indicator metric is relative abundance, which is annual abundance expressed as a percentage of the baseline:
relative abundance = annual abundance / baseline abundance
It is preferable to set baselines objectively, using one of the methods recommended by ICES (2015). But most Contracting Parties did not provide baselines in 2016. As an alternative, relative abundance was calculated using a baseline equal to the abundance at the start of the time series (i.e. 1992).
Species Selection and Aggregation (Functional Groups)
There were sufficient data to construct species-specific indicators of relative breeding abundance for the following 32 species: Arctic skua, Arctic tern, Atlantic puffin, black guillemot, black-headed gull, black-legged kittiwake, common eider, common guillemot, common gull, common tern, Eurasian spoonbill, European shag, great black-backed gull, great cormorant, great skua, herring gull, Kentish plover, lesser black-backed gull, little tern, mallard, Mediterranean gull, mute swan, northern fulmar, northern gannet, oystercatcher, pied avocet, razorbill, red-breasted merganser, ringed plover, roseate tern, Sandwich tern, and shelduck.
There were sufficient data to construct species-specific indicators of relative non-breeding abundance for the following 57 species: barnacle goose, bar-tailed godwit, Bewick’s swan, black guillemot, black-headed gull, black-tailed godwit, Brent goose, Canada goose, common eider, common gull, common merganser, common scoter, coot, dunlin, Eurasian curlew, Eurasian spoonbill, European shag, goldeneye, golden plover, great black-backed gull, great cormorant, great crested grebe, greater scaup, Greenland white-fronted goose, greenshank, grey plover, herring gull, king eider, lapwing, long-tailed duck, mallard, mute swan, oystercatcher, pied avocet, pintail, pochard, purple sandpiper, red-breasted merganser, red knot, red-necked grebe, redshank, red-throated diver, ringed plover, ruff, sanderling, shelduck, shoveler, Slavonian grebe, smew, spotted redshank, teal, tufted duck, turnstone, velvet scoter, whimbrel,whooper swan and wigeon.
Species were assigned to the functional groups given in Table a. The species assessed and the functional groups to which they were assigned, are given in Table b.
|Functional group||Typical feeding behaviour||Typical food types||Additional guidance|
|Wading feeders||Walk/wade in shallow waters||Invertebrates (molluscs, polychaetes, etc.)||None|
|Surface feeders||Feed within the surface layer (within 1 to 2 m of the surface)||Small fish, zooplankton and other invertebrates||“Surface layer” defined in relation to normal diving depth of plunge-divers (except gannets)|
|Water column feeders||Feed at a broad depth range in the water column||Pelagic and demersal fish and invertebrates (e.g. squid, zooplankton)||Include only species that usually dive by actively swimming underwater; but including gannets. Includes species feeding on benthic fish (e.g. flatfish).|
|Benthic feeders||Feed on the seafloor||Invertebrates (e.g. molluscs, echinoderms)||None|
|Grazing feeders||Grazing in intertidal areas and in shallow waters||Plants (e.g. eelgrass, saltmarsh plants), algae||Geese, swans and dabbling ducks, coot|
Species-specific assessment values
This assessment uses two different assessment values that are designed to reflect the resilience of different species to declines in their population (see ICES, 2008, 2010, 2011). It is desirable for the annual relative abundance of a species to be above, either:
- 0.8 (i.e. 80% of the baseline) – for species that lay one egg; or
- 0.7 (i.e. 70% of the baseline) – for species that lay more than one egg.
The reason for having two assessment values is because species that lay only one egg are expected to recover more slowly from declines in population size than species that can potentially produce more than one chick per year. If relative abundance is below the appropriate assessment value, it is considered to be in ‘poor’ status and further research and / or management is recommended, depending on what is appropriate.
An upper assessment value of 1.3 (i.e. 130% of the baseline) was applied to the annual relative abundance of all species. This upper assessment value is used to identify potentially disruptive increases in some species that might impact on other species (ICES, 2008). For instance, large predatory seabird species have benefited from the provision of food from fishery discards. The increase in numbers of species such as great black-backed gull and great skua have, in some areas, led to declines in species such as kittiwake that they prey on. However, this has the potential to wrongly identify a species as having a detrimental impact on other species when in fact it is in recovery to levels in excess of the baseline (ICES, 2010, 2011, 2013b). As a result, this upper assessment value is not used as an indicator of status and is only used to provide a trigger for further research and / or management, if increases in one species are likely to result in decreases in others.
Integration of species-specific assessments
The status of marine bird communities was assessed by calculating the proportion of species exceeding the lower assessment values, as previously used for breeding seabirds in the EcoQO on seabird population trends as an index of community health (ICES, 2008), according to the following integration rule:
Changes in abundance of marine birds should exceed species-specific assessment values in 75% or more of species that are assessed.
Humphreys et al. (2012) also recommended a value of 75% for non-breeding shorebirds and coastal breeding waterbirds in the United Kingdom because it is comparable to the assessment values used for shorebirds by the WeBS Alerts system.
In this indicator assessment, relative breeding abundance and relative non-breeding abundance were assessed separately. This is because most species in the breeding assessment are seabirds that use the wider marine environment and most species in the non-breeding assessment use intertidal and inshore areas. The breeding and non-breeding assessments therefore indicate impacts from different suites of pressures, operating in different parts of the marine environment.
To provide greater insight into the likely impacts operating on relative breeding abundance and on relative non-breeding abundance, species-specific assessments were integrated at different spatial scales: for each OSPAR Region and for each sub-division of the Greater North Sea and Arctic Waters. Within each Region, species-specific assessments were also integrated for each functional group (Table a).
Le pourcentage de toutes les espèces dans chaque groupe fonctionnel dépassant les valeurs d’évaluation pour l’abondance relative des reproducteurs et pour l’abondance relative des non-reproducteurs en 2014 dans la mer du Nord au sens large et en 2015 dans d’autres Régions OSPAR est indiqué dans le Tableau 1.
Dans les trois Régions OSPAR évaluées, moins de 75% de toutes les espèces évaluées dans tous les groupes fonctionnels atteignent les valeurs d’évaluation pour l’abondance relative des reproducteurs (Tableau 1), ce qui indique que les communautés d’oiseaux ne sont pas en bonne santé. Ceci s’applique également à l’abondance relative des non-reproducteurs dans la partie norvégienne des eaux arctiques et des mers Celtiques. En revanche, les valeurs d’évaluation sont atteintes pour l’abondance des non-reproducteurs pour plus de 75% des espèces dans la mer du Nord au sens large en 2014 (Tableau 1), ce qui s’est produit chaque année depuis 1993, à l’exception de 2010 (Figure 2).
La Figure 1 (abondance relative des reproducteurs) et la Figure 2 (abondance relative des non-reproducteurs) montrent les modifications du pourcentage annuel des espèces atteignant les valeurs d’évaluation depuis le début des années 1990. On a relevé un déclin de la proportion des espèces atteignant les valeurs d’évaluation depuis le milieu des années 2000 ou plus tôt dans toutes les Régions OSPAR évaluées.
La méthodologie et les données utilisées dans cette évaluation inspirent une confiance modérée.
Tableau 1: Pourcentage des espèces évaluées ayant une abondance relative supérieure aux valeurs d’évaluation dans chaque groupe fonctionnel dans la partie norvégienne des eaux Arctiques et dans les mers Celtiques en 2015 et dans la mer du Nord au sens large en 2014
The individual species that have failed to meet assessment values are shown in red in Figure b (breeding abundance) and Figure c (non-breeding abundance). There were few species for which breeding and non-breeding abundance could both be assessed: five in the Arctic Waters, 14 in the Greater North Sea and only one in the Celtic Seas. (see Figures b and Figure c).
The species-specific trends in breeding abundance and non-breeding abundance on which this indicator assessment are based, are shown in Figure d and Figure e. Trends were estimated at various spatial scales (i.e. OSPAR Regions and for sub-divisions thereof), depending on there being sufficient data available, for which the trends were estimated for each species.
The assessments of each species in 2014 or 2015 that were presented in Figure c are broken down into the sub-divisions of the Greater North Sea in Figure f and Figure g and in the sub-divisions of the Arctic Waters in Figure h and Figure i. The number of species included in the sub-divisional assessments are fewer than those in the regional assessments, because there are fewer colonies and sites at the smaller scale that have data from a sufficient number of years
The species-specific trends in relative breeding abundance in each OSPAR Region and sub-division (as shown in Figure a) during the period 1992–2015 can be downloaded here (Figures d1 to d29). The baseline is where relative abundance = 1.0. The black dotted line indicates the lower assessment value of 0.7 (for species that lay >1 egg) or 0.8 for species that lay 1 egg only); the black dashed line indicates the upper assessment value of 1.3. A list of the species by figure number is as follows: Figure d1 Arctic skua, Figure d2 Arctic tern, Figure d3 Black Guillemot, Figure d4 Black-headed Gull, Figure d5 Black-legged kittiwake, Figure d6 Brünnich’s guillemot, Figure d7 Common Eider, Figure d8 Common Guillemot, Figure d9 Common Gull, Figure d10 Common tern, Figure d11 Eurasian spoonbill, Figure d12 European shag, Figure d13 Glaucous gull, Figure d14 Great Black-backed Gull, Figure d15 Great Cormorant, Figure d16 Great Skua, Figure d17 Herring gull, Figure d18 Kentish plover, Figure d19 Lesser black-backed gull, Figure d20 Little Auk, Figure d21 Little Tern, Figure d22 Mallard, Figure d23 Manx Shearwater, Figure d24 Mute swan, Figure d25 Northern Fulmar, Figure d26 Northern gannet, Figure d27 Oystercatcher, Figure d28 Pied avocet, Figure d29 Puffin, Figure d30 Razorbill, Figure d31 Red-breasted merganser, Figure d32 Ringed plover, Figure d33 Roseate tern, Figure d34 Sandwich tern, Figure d35 Shelduck.
The species-specific trends in relative non-breeding abundance in each OSPAR Region and sub-division (as shown in Figure a) can be downloaded here (Figures e1 to e29). Trends for Norwegian parts of the Artic Waters and the Celtic Seas are are derived from counts in January of each year during 1992-2015. Data for all parts of the Greater North Sea are only available for the period 1992–2013. Trends for Greater North Sea sub-division d are derived from the annual mean of counts conducted throughout the year (July–June) from 1992/93 to 2013/14. The trends for the other Greater North Sea sub-divisions (i.e. a-c, e, f -see Figure a) are derived from counts in January of each year during 1992-2013. The baseline is where relative abundance = 1.0. The black dotted line indicates the lower assessment value of 0.7 (for species that lay >1 egg) or 0.8 (for species that lay 1 egg only); the black dashed line indicates the upper assessment value of 1.3.
A list of the species by figure number is as follows: Figure e1 Barnacle Goose, Figure e2 Bar-tailed Godwit, Figure e3 Bewicks Swan, Figure e4 Black Guillemot, Figure e5 Black-Headed Gull, Figure e6 Black-tailed Godwit, Figure e7 Brent Goose, Figure e8 Common Eider, Figure e9 Common Gull, Figure e10 Common merganser, Figure e11 Common Scoter, Figure e12 Coot, Figure e13 Curlew, Figure e14 Curlew Sandpiper, Figure e15 Dunlin, Figure e16 Eurasian spoonbill, Figure e17 Golden plover, Figure e18 Goldeneye, Figure e19 Great Black-Backed Gull, Figure e20 Great Cormorant, Figure e21 Great crested grebe, Figure e22 Greater Scaup, Figure e23 Greenshank, Figure e24 Grey Plover, Figure e25 Herring Gull, Figure e26 Kentish Plover, Figure e27 King eider, Figure e28 Lapwing, Figure e29 Little Egret, Figure e30 Long-tailed Duck, Figure e31 Mallard, Figure e32 Mute Swan, Figure e33 Oystercatcher, Figure e34 Pied avocet, Figure e35 Pintail, Figure e36 Pochard, Figure e37 Purple sandpiper, Figure e38 Red Knot, Figure e39 Red-breasted Merganser, Figure e40 Red-necked Grebe, Figure e41 Redshank, Figure e42 Red-throated diver, Figure e43 Ringed plover, Figure e44 Ruff, Figure e45 Sanderling, Figure e46 Shag, Figure e47 Shelduck, Figure e48 Shoveler, Figure e49 Slavonian grebe, Figure e50 Smew, Figure e51 Spotted Redshank, Figure e52 Teal, Figure e53 Tufted Duck, Figure e54 Turnstone, Figure e55 Velvet Scoter, Figure e56 Whimbrel, Figure e57 White-fronted goose, Figure e58 Whooper Swan, Figure e59 Wigeon.
There is moderate confidence in the methodology. There is consensus within the scientific community regarding this methodology, which was developed for the OSPAR EcoQO for seabird population trends, but it has not often been applied. There was also moderate confidence in the data. The assessment is undertaken using data with a mostly sufficient spatial coverage for the area assessed, but gaps are apparent in certain areas.
Depuis le milieu des années 2000, l’abondance des reproducteurs de plus d’un quart des espèces d’oiseaux de mer évalués dans la Zone maritime a été inférieure à la ligne de base déterminée en 1992, ce qui indique que les populations ne sont pas en bonne santé. On retrouve la même tendance dans l’abondance des non-reproducteurs des espèces visitant les eaux arctiques et les mers Celtiques durant la migration et / ou l’hivernage. En revanche, les populations de non-reproducteurs dans la mer du Nord au sens large se portent beaucoup mieux et on considère qu’elles sont en bonne santé, au moins 75% des espèces atteignant les valeurs d’évaluation chaque année depuis 1993.
La majorité des populations de reproducteurs évalués étaient des oiseaux de mer se nourrissant au large, principalement de poisson. Les espèces se nourrissant de poisson dans la colonne d’eau se portent beaucoup mieux que celles se nourrissant en surface. Ceci suggère que la disponibilité des espèces de petits poissons de fourrage en surface limite probablement le succès de la reproduction de certaines espèces. Les moteurs de la disponibilité de la nourriture sont probablement des modifications propres aux écosystèmes, éventuellement dues aux activités de pêche passées et présentes conjuguées au changement climatique.
Les populations de non-reproducteurs évalués appartiennent à cinq groupes fonctionnels d’oiseaux de mer, la majorité d’entre eux étant des barboteurs. Les évaluations de l’abondance des non-reproducteurs révèlent peu de différences entre les groupes fonctionnels.
The findings of this assessment relating to the importance of small forage fish species (e.g. lesser sandeel, sprat) at the surface of the sea as a limiting factor for breeding of some species (e.g. black-legged kittiwake, Rissa tridactyla) concurs with the results of the Common indicator on marine bird breeding success / failure.
Lacunes des connaissances
L’évaluation de cet indicateur pourrait également s’appliquer au golfe de Gascogne et à la côte ibérique et aux oiseaux de mer se reproduisant dans les Açores, si les données correspondantes des Parties contractantes sont disponibles. Les données pour l’évaluation des eaux Arctiques sont absentes. L’évaluation de cet indicateur pourrait également être élargie pour inclure plus de données sur les oiseaux de mer et les oiseaux aquatiques recueillies en mer.
Les lignes de base utilisées dans l’évaluation de cet indicateur ont été attribuées au début de la série de données évaluées. Il serait plus objectif de déterminer des lignes de base comprenant des « niveaux de référence historiques », qui reflètent l’abondance à un certain moment du passé longtemps avant le début des séries temporelles ou des « niveaux de référence » lorsque l’on présume que les impacts anthropiques sur la taille des populations sont négligeables.
Expansion of the indicator to other OSPAR Regions
Of the 21 marine bird species breeding in the Bay of Biscay and Iberian Coast region, nine occur in very low numbers, and with no monitoring data collected for two (Cory’s shearwater, Calonectris diomedea and band-rumped storm-petrel, Oceanodroma castro) (ICES, 2008). Data quality for six of the 10 remaining species was assessed as ‘good’, three were assessed as ‘sparse’, and data quality for one (little tern, Sternula albifrons) breeding in Portugal was unknown (ICES, 2008).
The Azores are currently working with the other Macaronesian archipelagos (Madeira and the Canary Islands) to establish a common monitoring plan for breeding seabirds within the framework of the MISTIC Seas Project (European Union funded). This plan will be implemented, with the support of a recently granted European Union Project MISTIC SEAS II, and will enable the collection of data on seabird abundance.
Inclusion of at-sea data
Data on seabirds at sea, collected from boats or planes, were not included in the abundance indicator. However, these data need to be included in the future to obtain reliable results on trends in species that occur in substantial numbers offshore. At present, several Contracting Parties carry out, or plan to carry out, national at-sea monitoring programmes. Elsewhere, there are either no at-sea surveys or those that do exist are very limited in spatial and temporal coverage. Overall, coordination of surveys (e.g. regarding timing) between countries is lacking. There is a need to develop a concept for joint survey efforts delivering the necessary data basis for the abundance indicator work, to implement this concept in the frame of national survey programmes in future years, and to develop a methodological approach for aggregating and analysing the data.
Most Contracting Parties did not provide baselines in 2016. As an alternative, relative breeding abundance was calculated using a baseline equal to the abundance in the second year of the time series (i.e. 1992). ICES (2015) recommended that it is preferable to set baselines objectively, using one of the methods (a) or (b), below.
- 'Historical reference’: where abundance is known at a point in the past long before the time series began, but where the reasons for subsequent change are unknown. Historical population estimates should be used as baselines if they were recorded: before known human impacts; and / or before other major declines in population; or at known plateaus in population trends, following increases and peaks in population size.
- ‘Reference level’: the population size that could be expected if human impacts were negligible (this can be derived from known population sizes either historically or from within available time series). Use of the highest known population estimate when the population has decreased in size, as a result of human impacts (e.g. periods of severe contamination) or following stochastic natural impacts (e.g. severe weather events). Use of recent population estimates (e.g. previous five-year mean) when a species has been colonising.
ICES. 2008. Report of the Workshop on Seabird Ecological Quality Indicator, 8–9 March 2008, Lisbon, Portugal. ICES CM 2008/LRC:06. 60 pp.
ICES. 2010. Report of the Working Group on Seabird Ecology (WGSE). 15–19 March 2010, Copenhagen. ICES CM 2010/SSGEF:10. 81 pp.
ICES. 2011. Report of the Working Group on Seabird Ecology (WGSE). 1–4 November 2011, Madeira, Portugal. ICES CM 2011/SSGEF:07. 77 pp.
ICES. 2012. ICES advice on EcoQO for seabird populations in OSPAR regions II and III. In Report of the ICES Advisory Committee, 2012. ICES Advice 2012, Book 1, Section 184.108.40.206. Also available as a separate advice sheet at: http://www.ices.dk/sites/pub/Publication%20Reports/Advice/2012/Special%20Requests/OSPAR_EcoQO_for_seabird_populations.pdf
ICES. 2013a. OSPAR request on ecological quality objective for seabird populations in OSPAR Region III (Celtic seas). In Report of the ICES Advisory Committee, 2013. ICES Advice 2013, Book 1, Section 220.127.116.11. Also available as a separate advice sheet at: http://www.ices.dk/sites/pub/Publication%20Reports/Advice/2013/Special%20requests/OSPAR_EcoQO_region_III.pdf
ICES. 2013b. Report of the ICES Ad hoc Group on Seabird Ecology (AGSE), 28–29 November 2012, ICES Headquarters, Copenhagen, Denmark. ICES CM 2012/ACOM:82. 30 pp.
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ICES. 2013d. OSPAR request on an update of the ecological quality objective (EcoQO) on seabird population trends. In Report of the ICES Advisory Committee, 2013. ICES Advice 2013, Book 1, Section 18.104.22.168.
ICES. 2015. Report on the Joint ICES/OSPAR Working Group on Seabirds (JWGBIRD), 17-21 November 2014, Copenhagen, Denmark. ICES CM 2014/ACOM:30, 115 pp.
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