Eutrophication is caused by excessive inputs of nutrients (nitrogen and phosphorus) resulting from various human activities. High concentrations of nutrients and the ratios of these nutrients (e.g. N:P stoichiometric ratios) form the preconditions for algal growth, reduced water clarity and increased oxygen consumption. Long-term nutrient data are key parameters for quantifying the effects of anthropogenic activities and evaluating the success of measures undertaken since they directly link to increased nutrient inputs.

Eutrophication assessment

The status of eutrophication is assessed using several core indicators. Each indicator focuses on one important aspect of the complex issue.​ In addition to providing an indicator-based evaluation of total nitrogen, this indicator contributes to the overall eutrophication assessment along with the other eutrophication core indicators.​

2.1 Ecological relevance

Role of total nitrogen (TN) in the ecosystem

Marine eutrophication is mainly caused by nutrient enrichment, leading to increased production of organic matter in the Baltic Sea, with subsequent effects on water transparency, phytoplankton communities, benthic fauna and vegetation, as well as oxygen conditions. Phytoplankton as well as benthic vegetation need nutrients, mainly nitrogen and phosphorus, for growth. Adding total nutrients alongside inorganic nutrients as core indicators strengthens the link from nutrient concentrations in the sea to nutrient enrichment. In particular these parameters allow to take account of climate change in the eutrophication assessment since higher temperatures will lead to year-round phytoplankton proliferation and / or possible changes in zooplankton communities.

In a simplified conceptual model for nitrogen and phosphorus nutrients (Relevance figure 1), flows between the different components are illustrated. To get a good understanding of the trend in nutrient concentrations in the marine environment the assessment of both, total and dissolved nutrients, is important. In contrast to dissolved inorganic nitrogen (DIN), total nitrogen is a parameter not subject to strong seasonal fluctuations and reflects a more or less stable situation during the year, allowing a reliable annual average to be calculated for surface water (0-10 m). Total nitrogen comprises dissolved inorganic nitrogen components and nitrogen already bound in organic matter, including algae and bacteria. A significant portion of TN is refractory. A simplified assumption is that nitrogen stays in the system, and is basically converted between the inorganic dissolved and the organic reservoir (without taking sedimentation into account). Thus, an approximately stable situation can be assumed over the year and a reliable annual average for the surface water (0-10 m) can be calculated.

Figure 2. Simplified conceptual model for N and P nutrients in the Baltic Sea, where DIN = Dissolved inorganic nitrogen, TN = Total nitrogen, DIP = Dissolved inorganic phosphorus and TP = Total phosphorus. Flows along arrows into the blue sea area tend to increase concentrations, and flows along arrows out from the sea act in the opposite direction. Management refers to nutrient load reductions.

2.2 Policy relevance

Eutrophication is one of the thematic segments of the HELCOM Baltic Sea Action Plan (BSAP). HELCOM BSAP has a strategic goal of a Baltic Sea unaffected by eutrophication (HELCOM 2021). Eutrophication is defined in the BSAP as a condition in an aquatic ecosystem where high nutrient concentrations stimulate the growth of algae, which leads to imbalanced functioning of the system. Elevated nutrient concentrations in the water column are caused by increased anthropogenic nutrient loads from land and air. The goal for eutrophication is broken down into five ecological objectives, of which one is “concentrations of nutrients close to natural levels”. The BSAP management objective is to “minimize inputs of nutrients from human activities”.

The EU Marine Strategy Framework Directive (2008/56/EC) requires that “human-induced eutrophication is minimized, especially adverse effects thereof, such as losses in biodiversity, ecosystem degradation, harmful algal blooms and oxygen deficiency in bottom waters” (Descriptor 5). ‘Nutrients in the water column’ (including TN) are one of the criteria elements in MSFD GES Decision ((EU) 2017/848) for assessing eutrophication under the criterion ‘D5C1 – Nutrient concentrations are not at levels that indicate adverse eutrophication effects’.

The EU Water Framework Directive (2000/60/EC) requires good ecological status in the European coastal waters. Good ecological status is defined in Annex V of the Water Framework Directive, in terms of the quality of the biological community, the hydrological and the chemical characteristics, including nitrogen concentration.

Table 1. Eutrophication links to policy.

2.3 Relevance for other assessments

This indicator is utilised in the integrated assessment of eutrophication (HEAT tool).

Status is evaluated in relation to scientifically based and commonly agreed sub-basin specific threshold values, which define the concentration that should not be exceeded (Table 2 and Table 3).

Figure 3. Schematic representation of the threshold values applied in the TN core indicator, the threshold values are assessment unit specific (see Table 2).

3.1 Setting the threshold value(s)

Indicator threshold values were based on the results obtained in the TARGREV project (HELCOM 2013), also taking advantage of the work carried out during the EUTRO PRO process (HELCOM 2009) and national work for EU WFD. The final threshold values were set through an expert evaluation process done via intersessional activity to develop core eutrophication indicators (HELCOM CORE EUTRO), and the threshold values were adopted by the HELCOM Heads of Delegations 39/2012. The threshold values were principally not changed since HOLAS II, but for the new assessment units Pomeranian Bay and the split of the Gulf of Finland into an eastern and western assessment unit new thresholds were derived using the HOLAS II thresholds as a basis and adopted by HELCOM HOD 61-2021. The newly agreed threshold values for Kiel Bay, Bay of Mecklenburg and Arkona Basin are based on a national modelling approach and in line with the general approach in the eutrophication assessment to choose the most precautionary target.

Table 2. Assessment unit specific threshold values for total nitrogen.

The results of the indicator evaluation that underlying the key message map and information are provided below.

4.1 Status evaluation

Current status of the Baltic Sea TN concentration

TN concentrations below the threshold were achieved in three western assessment units, the Kattegat, Great Belt and Kiel Bay (Figure 4 and Table 3). Accordingly, the scaled Ecological quality ratio (EQRS) was 0.67 for Kattegat, 0.72 for Kiel Bay and 0.80 for Great Belt, resulting in achieving good status. In the remaining 16 sub-basins, achieving the threshold value failed, resulting in a not good status. Two assessment units showed TN concentrations exceeding the threshold value by more than 50%, the Eastern Gotland Basin and the Pomeranian Bay with EQRS values below 0.30, but still above 0.20, indicating poor status. Pomeranian Bay is heavily influenced by nitrogen inputs from the river Odra. Another four sub-basins with TN concentrations between 30% and 40% above the threshold value were Bornholm Basin, Gdansk Basin, Western Gotland Basin and Northern Baltic Proper with EQRS values of 0.33 to 0.38 reflecting a poor status. In the Gulf of Finland Western the threshold was exceeded by 25% resulting in a moderate status classification based on the EQRS value of 0.42. A minor exceedance of the threshold for TN between 10% and 15% was found in the Åland Sea and the Gulf of Finland Eastern with respective EQRS values of 0.49 and 0.50 indicating a moderate status. In seven sub-basins (The Sound, Bay of Mecklenburg, Arkona Basin, Gulf of Riga, Bothnian Sea, The Quark and Bothnian Bay), a very minor exceedance of the threshold value for TN below 10% was observed with EQRS values between 0.52-0.59, indicating a still moderate status, but very close to the threshold value. All EQRS values were related to the good/moderate boundary of 0.6 to evaluate if TN concentrations were below or above the threshold.

The variability of the TN concentrations between the individual assessment years is shown in Figure 5. The variability was largest in the Pomeranian Bay, indicating the strong influence of the Odra river plume. In general, smaller assessment units that are more strongly influenced by riverine nutrient inputs and have higher TN concentrations, show a larger variability between the years. In Kiel Bay, TN concentrations exceeded the threshold value in 2021, but were well below the threshold in all other years.

Figure 4. Detailed eutrophication assessment with the ecological quality ratio scaled (EQRS). EQRS of total nitrogen being split into 5 classes to show a more differentiated picture than the 2-class division used in the key message figures. EQRS is calculated as the ratio of the average concentration during assessment period and the reference value, decreasing along with increasing eutrophication. When EQRS ≥ 0.6 good status is achieved.

Figure 5. Average annual surface total nitrogen concentrations (dashed dark blue line; average for 2016-2021) in µmol L^-1 and threshold levels as agreed by HELCOM HOD 39-2012 or HELCOM HOD in 2022 via correspondence (green line) for assigned Assessment Units (AU).

Table 3. Threshold values, present concentration (as average 2016-2021), Ecological quality ratio scaled (EQRS) and status of total nitrogen in the open-sea basins. EQRS is calculated as the ratio of the average concentration during the assessment period and the reference value. Please note that coastal areas shown are from national reporting and can reflect annual or summer data (see Table 4 for details).

Concerning the coastal waters TN was assessed in Estonian, Finnish, German, Polish and Swedish waters. In German coastal waters five out of the 43 water bodies assessed achieved good status. In Finnish coastal waters five out of 12 water bodies were assessed as good, while in Estonian waters five out of 14 water bodies achieved good status. In Polish waters two water bodies out of 19 reached good status. In Swedish coastal waters, TN assessments were carried out for different seasons (summer and winter). Out of 19 water bodies with two potential assessment results each for summer and winter, 11 assessment results indicated good status, either for summer or winter. The majority of assessment areas in good status was achieved for total nitrogen in winter (eight assessment areas), while only three assessment areas achieved good status in summer. Only in Kattegat West Coast outer coastal waters, good status was achieved in both seasons for total nitrogen.

4.2 Trends

Long-term trends

Long-term temporal trends allow to evaluate the actual six-years assessment period in its annual changes compared to previous evaluation periods and to previous decades. Moreover, they provide an impression what can be expected for the near future and perhaps when thresholds will be met or concentrations fall below the thresholds in the future. Data of TN concentrations are presented for all assessment units for the extended time period of 50 years in Results figure 3, with the exception of the Gulf of Riga, where TN data are only available since 1990, and considerable data gaps in the Pomeranian Bay between 1980 and 1995. Significant improving trends (decreasing TN concentrations) since the 1990s were documented for the assessment units of Kattegat, Great Belt, The Sound, Kiel Bay, Bay of Mecklenburg, Gulf of Riga, Nortern Baltic Proper, Gulf of Finland Western and Eastern, Åland Sea, The Bothnian Sea, The Quark and Bothnian Bay. Deteriorating trends (increasing TN concentrations) were observed in the Bornholm Basin, Pomeranian Bay, Gulf of Gdansk and the Eastern Gotland Basins, while other areas showed a relative stable situation during the recent decades in Arkona Basin and Western Gotland Basin. In the current assessment period of the last six years, a declining trend of total nitrogen can be deduced for the Bothnian Bay and the Kattegat, while increasing concentrations were detected for Bay of Mecklenburg, Northern Baltic Proper, Gulf of Finland Western and Eastern and the Åland Sea. All other assessment units showed more or less inter-annual variability without a clear tendency or trend. Kattegat, Great Belt and Kiel Bay were below the threshold and achieved good status, while Arkona Basin, Bay of Mecklenburg and The Quark were closest to the threshold, but still in not good status. All others sub-basins were above the aimed threshold values as indicated by the green line in Figure 6.

Figure 6. Temporal development of total nitrogen (TN) concentrations in the open-sea assessment units in 1970-2016. Dashed lines show the five-year moving averages and error bars the standard deviation. Green lines denote the indicator threshold. Significance of trends was assessed with Mann-Kendall non-parametric tests for the period from 1990-2021. Significant (p<0.05) improving trends are indicated with blue, deteriorating trends with orange data points and those without colour were insignificant.

4.3 Discussion text

Assessment results for TN concentrations (as EQRS values) were compared between the latest two assessments of HOLAS II and HOLAS 3 (Table 4). One status change was observed between the two assessment periods in Kiel Bay, where good status was achieved in HOLAS 3. The majority of assessment units (16 out of 19 assessment units) showed no distinct change (within 15% change between HOLAS II and 3), with about half of the assessment units showing decreasing EQRS values (i.e. increasing TN concentrations meaning further deterioration) in the Northern Baltic Proper, Western Gotland Basin, Gulf of Riga, Gulf of Finland and The Sound, while increasing EQRS values were observed for the other half of the assessment units, indicating an improvement. In the Gdansk Basin increasing EQRS values were close to the 15% change boundary, indicating a clearly improving status for TN concentrations. In Eastern Gotland Basin a distinct negative change of about 20% was observed with decreasing EQRS values (i.e. increasing TN concentrations) of the already poor status classification. In the Bay of Mecklenburg and Kiel Bay distinct positive changes were detected between the two assessment periods, indicating improving conditions, which have already led to achieving good status in Kiel Bay.

Table 4. Comparison of TN EQRS values between HOLAS II and HOLAS 3 (coloured red or green depending on whether the assessment unit achieves or fails to achieve good status) and a description of the trend observed (distinct change when >15%).

The overall confidence of the indicator is based on the temporal confidence, spatial confidence and accuracy of the monitoring data for the assessment period 2016-2021 carried out in the HEAT tool. In general, the aspect of temporal coverage of monitoring data considers the confidence of the indicator in terms of its year-to-year variation and the continuity of observations during the indicator-specific assessment season, in this case the entire year from January to December. The general temporal confidence (GTC) is assessed based on the number of annual observations during the assessment period, whereas for the specific temporal confidence (STC) the number of missing months in the respective assessment season (entire year) determines the classification. The specific spatial confidence (SSC) evaluates the spatial representability of the monitoring data and is based on a gridded approach. Lastly, the accuracy confidence (ACC) indicates how certain the assessment is in relation to the variability of the data to estimate the probability of correct classification in terms of failing or achieving good status. To combine the different confidence assessments GTC and STC are averaged to an overall result for temporal confidence and this result is then averaged with SSC and subsequently combined with ACC to obtain a result for the indicator.

The overall confidence of the indicator status evaluation in open sea areas, based on the spatial and temporal coverage of data and the accuracy of the classification results was high in the Kattegat, Kiel Bay, Bay of Mecklenburg, Arkona and Bornholm Basin, Western and Eastern Gotland Basin, Gulf of Riga, Northern Baltic Proper and Gulf of Finland Western. The overall confidence was moderate in Great Belt and The Sound, Pomeranian Bay, Gdansk Basin, Gulf of Finland Eastern, Bothnian Sea, The Quark and Bothnian Bay. Only in Åland Sea the overall confidence was low (see results figure 4). Looking at the different components of the overall confidence assessment separately (results figure 5), the accuracy of the assessment was high for all assessment units indicating correct classifications with a probability >90%. Selected assessment units showed a moderate to low temporal confidence and the spatial confidence was overall assessed to be worst, with a larger number of assessment units showing a moderate or low spatial confidence, necessitating an increase and better spread of monitoring stations (see Figure 8). High spatial confidence was only achieved in the Kattegat, Bay of Mecklenburg, Arkona Basin, Gulf of Riga and Gulf of Finland Western.

Confidence was assessed in all open sea assessment units, but not in coastal waters.

Figure 7. Overall indicator confidence (C), determined combining information on data availability and the accuracy of the classification for failing or achieving good status. Low indicator confidence calls for increase in monitoring.

Figure 8. Confidence maps for accuracy class confidence (ACC), spatial confidence (SC) and temporal confidence (TC).

For HOLAS 3 initial work has been carried out to explore Drivers (and driver indicators) to evaluate how such information can be utilised within such management frameworks as DAPSIM. Although it is recognised as only addressing a small portion of the drivers (via proxies) of relevance for eutrophication wastewater treatment (Drivers and driver indicators for Wastewater Treatment) and agriculture (Drivers and
driver indicators for Agricultural Nutrient Balance) have been explored in these pilot studies for HOLAS 3.

Nutrient concentrations in the water column are affected by increased anthropogenic nutrient loads from land and air. Diffuse sources constitute the highest proportion of total nitrogen (nearly 50%) inputs to the Baltic Sea (HELCOM 2022). For total nitrogen, atmospheric deposition on the sea has the second highest share (24%) followed by natural background loads (20%) and point sources (9%). The importance of the four sources varies between the different sub-basins. Point sources include activities such as municipal wastewater treatment plants, industrial plants and aquacultural plants and diffuse sources consist of natural background sources, and anthropogenic sources as agriculture, managed forestry, scattered dwellings, storm water etc.

A significant reduction of nutrients input has been achieved for the whole Baltic Sea. The normalized total input of nitrogen was reduced by 12% between the reference period (1997-2003) and 2020 (HELCOM 2023). The maximum allowable input (MAI) of nitrogen in this period was fulfilled in the Bothnian Bay, Bothnian Sea, Danish Straits and Kattegat. This has, however, not yet resulted in a good status of tota nitrogen concentrations in these basins, as demonstrated in this indicator assessment, indicating the delay in recovery processes from eutrophication and possibly the effects of internal nitrogen loads (Gustafsson et al. 2012).

Further developing an overview of such components and the relevant data to be able to better quantify the linkages within a causal framework provide the opportunity for more informed management decisions, for example targeting of measures, and can thereby support the achievement of Good Environmental Status.This indicator itself addresses the inputs of nutrients to the Baltic Sea (i.e. pressures) and a number of status indicator exist, thus an improved understanding of the relevant components related to drivers and activities (their data sources and how to evaluate them) can significantly improve the overall understanding of eutrophication and appropriate management of the issue.

Table 5. Brief summary of relevant pressures and activities with relevance to the indicator.

The current knowledge of the effects of climate change to eutrophication is summarized in the HELCOM climate change fact sheet (HELCOM andBaltic Earth 2021). The effect of climate change to the nutrient pools is not yet separable from the other pressures, and the future nutrient pools will dominantly be affected by the development of nutrient loading. The phytoplankton growth season has already prolonged due to changes in cloud cover and stratification. Climate change is, with medium confidence, considered to increase the stratification, further deteriorate near-bottom oxygen conditions, and increase the internal nutrient loading (Gustafsson et al. 2012). Climate change also leads to a higher variability in riverine nutrient inputs, with an increase of floods and droughts. Such extreme events might have a direct impact on the nutrient concentrations in the Baltic Sea.

The status evaluation fails to achieve good status in all assessed sub-basins except for Kattegat, Great Belt and Kiel Bay.

8.1 Future work or improvements needed

A better harmonisation of the thresholds for TN between coastal waters and the open Baltic Sea Basins might be necessary in the future, in particular in areas where coastal waters are already assessed as achieving good status while the open basins still fail to achieve good status, since such a gradient would not be expected to occur assuming that high nutrient concentrations are mainly caused by riverine nutrient inputs. In addition, a better understanding needs to be developed on how nutrient concentrations react to ongoing climate change and how they are influenced by extreme hydrological events (floods, droughts). Lastly, the interlinkages between nitrogen inputs and nitrogen concentrations in the sea also need to be better understood.

9.1 Scale of assessment

The core indicator is applicable in the 19 open sea assessment units (at least one nautical mile seawards from the baseline). In the coastal units, the indicator is assessed using comparable indicators developed nationally for the purposes of assessments under the EU Water Framework Directive.

The assessment units are defined in the HELCOM Monitoring and Assessment Strategy Annex 4.

9.2 Methodology applied

For the open sea assessment, this core indicator is updated using data reported by Contracting Parties to the HELCOM COMBINE database hosted by ICES, using the algorithms developed for the eutrophication assessment work flow. The values are achieved using indicators specifications shown in Table 6 (see HELCOM Eutrophication assessment manual).

Table 6. Specifications for the TN indicator.

9.3 Monitoring and reporting requirements

Monitoring methodology

Monitoring of nitrogen concentrations by the Contracting Parties of HELCOM is described on a general level in the HELCOM Monitoring Manual in the sub-programme Nutrients.

Monitoring guidelines ​specifying the sampling strategies for total nitrogen are adopted and published.

Current monitoring

The monitoring activities relevant to the indicator, as currently carried out by HELCOM Contracting Parties, are described in the HELCOM Monitoring Manual sub-programme Nutrients monitoring concepts table.

Description of optimal monitoring

Regional monitoring of total nitrogen is considered sufficient to support the indicator evaluation. Increased temporal and spatial monitoring in certain areas would further improve the confidence in future assessments.

The data and resulting data products (e.g. tables, figures and maps) available on the indicator web page can be used freely given that it is used appropriately and the source is cited.

Result: Total nitrogen (TN)​​​​​

Data source: The average for 2016-2021 was estimated using monitoring data provided by the HELCOM Contracting Parties, and kept in the HELCOM COMBINE database, hosted by ICES (www.ices.dk). Nominated members of HELCOM STATE & CONSERVATION group were given the opportunity to review the data, and to supply any missing monitoring observations, in order to achieve a complete dataset.

Description of data: The data include total nitrogen observations, determined as explained in the HELCOM monitoring manual. Measurements made at the depth of 0-10 m from the surface were used in the assessment.

Geographical coverage: The observations are distributed in the sub-basins according to the HELCOM monitoring programme, added occasionally with data from research cruises.

Temporal coverage: The raw data includes observations throughout the year, during the assessment period 2016-2021. For the summer average, observations taken during June-September were included only.

Data aggregation: The 2016-2021 averages for each sub-basin were produced as inter-annual estimates using observations from all months / June-September.

Birgit Heyden¹, Wera Leujak², Joachim Kuss³, Theodor Hüttel⁴, Joni Kaitaranta⁴, HELCOM Expert Group on Eutrophication (EG Eutro)

¹ AquaEcology, Germany

² German Environment Agency, Germany
³ Leibniz Institute for Baltic Sea Research Warnemünde (IOW), Germany

⁴ Secretariat of the Helsinki Commission

This version of the HELCOM core indicator report was published in April 2023:

The current version of this indicator (including as a PDF) can be found on the HELCOM indicator web page.

Total nitrogen (TN) HELCOM core indicator 2018 (pdf)

HOLAS II component – Core indicator report – web-based version July 2017 (pdf)

Nutrient concentrations 2003-2007 – HELCOM Core Indicator Report (pdf)

Gustafsson, B.G.; Schenk, F.; Blenckner, T.; Eilola, K. et al (2012): Reconstructing the Development of Baltic Sea Eutrophication 1850–2006. Ambio 41, pages 534-548

Directive 2000/60/EC of the European parliament and of the council of 23 October 2000 establishing a framework for community action in the field of water policy. Official Journal of the European Communities L 327/1.

Directive 2008/56/EC of the European Parliament and of the Council. 17 June 2008. Establishing a Framework for Community Action in the Field of Marine Environmental Policy. Marine Strategy Framework Directive. 22p.

HELCOM (2009) Eutrophication in the Baltic Sea – An Integrated Thematic Assessment of the Effects of Nutrient Enrichment and Eutrophication in the Baltic Sea Region. Balt. Sea Environ. Proc. No. 115B, 148.

HELCOM (2013) Approaches and Methods for Eutrophication Target Setting in the Baltic Sea Region. Balt. Sea Environ. Proc. No. 133.

HELCOM (2021) “Baltic Sea Action Plan. 2021 Update.” https://helcom.fi/wp-content/uploads/2021/10/Baltic-Sea-Action-Plan-2021-update.pdf.

HELCOM (2022) Assessment of sources of nutrient inputs to the Baltic Sea in 2017.” https://helcom.fi/wp-content/uploads/2022/12/PLC-7-Assessment-of-sources-of-nutrient-inputs-to-the-Baltic-Sea-in-2017.pdf

HELCOM (2023) “Inputs of Nutrients to the Sub-Basins (2023). HELCOM Core Indicator Report. Online.” 2023.

HELCOM and Baltic Earth (2021) Climate Change in the Baltic Sea. 2021 Fact Sheet. Baltic Sea Environment Proceedings N°180. https://doi.org/ISSN: 0357-2994.

HELCOM: First version of the ‘State of the Baltic Sea’ report – June 2017, Baltic Marine Environment Protection Commission – HELCOM, Helsinki, Finland, 197, 2017.

Eutrophication status of the Baltic Sea 2007-2011 – A concise thematic assessment​​ (2014)

Approaches and methods for eutrophication target setting in the Baltic Sea region (2013)

HELCOM core indicators. Final report of the HELCOM CORESET project (2013)

Eutrophication in the Baltic Sea. An integrated thematic assessment of the effects of nutrient enrichment in the Baltic Sea region​ (2009)

Development of tools for assessment of eutrophication in the Baltic Sea (2006)

The table below provides an overview of coastal data.

Annex providing an overview of additional coastal evaluations reported by Contracting Parties

Annex table 1. Results for national coastal Total Nitrogen indicators by coastal WFD water type/water body. The table includes information on the assessment unit (CODE, defined in the HELCOM Monitoring and Assessment Strategy Annex 4) and description, assessment period (start year and/or end year), threshold value (ET) in μmol/l with exceptions of 3002 and 7003-7004 indicator being measured in mg/l. Average concentration during assessment period (ES) in μmol/l with exceptions of 3002 and 7003-7004 indicator being measured in mg/l and standard deviation (SD), Ecological Quality Ratio (EQR) and Ecological Quality Ratio Scaled (EQRS). EQRS shows the present concentration in relation to the reference value, decreasing along with increasing eutrophication. EQRS_class estimates the ecological status based on the EQRS value.

Annex Table 2