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Indicator Assessment
Concentrations of BOD and total ammonium have decreased in European rivers in the period 1992 to 2010 (Fig. 1), mainly due to general improvement in wastewater treatment.
See also WISE interactive maps: Mean annual BOD in rivers and Mean annual Total Ammonium in rivers
Biochemical Oxygen Demand (BOD5) and total ammonium concentrations in rivers between 1992 and 2010
Note: Concentrations are expressed as annual mean concentrations. Only complete series after inter/extrapolation are included (see indicator specification). The number of river monitoring stations included per country is given in metadata (see downloads and more info). BOD7 data has been recalculated into BOD5 data.
BOD5 concentrations in rivers between 1992 and 2010 in different geographical regions of Europe
Note: The data series per region are calculated as the average of the annual mean for river monitoring stations in the region. Only complete series after inter/extrapolation are included (see indicator specification). The number of river monitoring stations included per geographical region is given in parentheses. BOD7 data has been recalculated into BOD5 data.
Total ammonium concentrations in rivers between 1992 and 2010 in different geographical regions of Europe
Note: The data series per region are calculated as the average of the annual mean for river monitoring stations in the region. Only complete series after inter/extrapolation are included (see indicator specification). The number of river monitoring stations included per geographical region is given in parentheses.
BOD5 concentrations in rivers between 1992 and 2010 draining to different sea regions of Europe
Note: The sea region data series are calculated as the average of annual mean data from river monitoring stations in each sea region. The data thus represents rivers or river basins draining into that particular sea. Only complete series after inter/extrapolation are included (see indicator specification). The number of river monitoring stations included per sea region is given in parentheses. There were no stations with consistent data series on BOD7 in rivers draining to the Arctic Ocean. BOD7 data has been recalculated into BOD5 data.
Total ammonium concentrations in rivers between 1992 and 2010 draining to different sea regions of Europe
Note: The sea region data series are calculated as the average of annual mean data from river monitoring stations in each sea region. The data thus represents rivers or river basins draining into that particular sea. Only complete series after inter/extrapolation are included (see indicator specification). The number of river monitoring stations included per sea region is given in parentheses.
Introduction
Organic matter, measured as Biochemical Oxygen Demand (BOD) and total ammonium, are key indicators of the oxygen content of water bodies. Concentrations of these parameters normally increase as a result of organic pollution caused by discharges from waste water treatment plants, industrial effluents and agricultural run-off. Severe organic pollution may lead to rapid de-oxygenation of river water, a high concentration of ammonia and the disappearance of fish and aquatic invertebrates.
The most important sources of organic waste load are: household wastewater; industries such as paper industries or food processing industries; and silage effluents and manure from agriculture. Increased industrial and agricultural production, coupled with a greater percentage of the population being connected to sewerage systems, initially resulted in increases in the discharge of organic waste into surface water in most European countries after the 1940s. Over the past 15 to 30 years, however, the biological treatment (secondary treatment) of waste water has increased, and organic discharges have consequently decreased throughout Europe. See also CSI 024: Urban waste water treatment.
Overall trend in BOD and total ammonium (Fig. 1)
In European rivers, the oxygen demanding substances measured as BOD and total ammonium have decreased by 55 % (from 4.9 mg/l to 2.2 mg O2/l) and 73 % (from 587 to 159 µg N/l), respectively, from 1992 to 2010 (Fig. 1). The decrease is due mainly to improved sewage treatment resulting from the implementation of the Urban Wastewater Treatment Directive and national legislations. The economic downturn of the 1990s in central and eastern European countries also contributed to this fall, as there was a decline in heavily polluting manufacturing industries. In recent years, however, the downward trends in BOD across Europe have generally levelled. This suggests that either further improvement in wastewater treatment is required or that other sources of organic pollution, for example from agriculture, require greater attention, or both.
Overall there has been a significant decrease in BOD concentrations at 56.8 % of the stations (an additional 6.1 % marginally significant) on the European rivers between 1992 and 2010, while there has been a significant increase at only 3.1 % of the stations (an additional 0.9 % marginally significant). Similarly, there has been a significant decrease in total ammonium concentrations at 56.4 % of the stations (an additional 7.0 % marginally significant), while there has been a significant increase at only 3.2 % of the stations (an additional 1.2 % marginally significant).
BOD and total ammonium time series and trends per geographical regions (Fig. 2 and Fig. 3)
The largest decrease of BOD from 1992 to 2010 has occurred in the southern and southeastern European rivers (63 % and 57 %, respectively) (Fig. 2). The concentrations in the southeastern European rivers are still the highest in Europe, but with a fall below 4 mg O2/l in 2010, which is the lowest level to date. The concentrations of the southern European rivers (represented by the Spanish rivers only) reached the lowest level in 2003. They increased afterwards to about 2.9 mg O2/l. The concentrations in the western European rivers decreased by 50 %. Their concentrations are the lowest in Europe (about 1.5 mg O2/l). The concentrations in the northern European rivers (represented by the Finnish rivers only) are the most stable (less than 2 mg O2/l) with a decrease of 22 %.
The largest proportion of monitoring stations with significant or marginally significant negative trend in BOD is found for the western and the southern European rivers, while the lowest proportion is found for the northern European rivers. Based on the sum of significant and marginally significant trends the trends for the rivers in different geographic regions are: West: 72.5 % negative, 0.6 % positive; South: 62.7 % negative, 2.8 % positive; East: 56.5 % negative, 9.0 % positive; Southeast: 50.0 % negative, 6.9 % positive; North: 33.3 % negative, 6.7 % positive. Countries with more than 60 % of the stations with negative trend in BOD are the United Kingdom, Spain, Luxembourg, the Czech Republic, Austria, Denmark, Slovakia, France, Slovenia and Ireland.
The decrease of total ammonium from 1992 to 2010 is the largest in the southeastern (77 %) and eastern European rivers (76 %), closely followed by the decrease in the western European rivers (74 %) (Fig. 3). The concentrations in the eastern European rivers (about 200 µg N/l) have approached the concentrations in the western European rivers (about 150 µg N/l). The lowest decrease has occurred in the southern European rivers (represented by Spanish rivers only) (20 %) and the northern European rivers (14 %). The concentrations in the first ones are very fluctuating and among the highest in Europe (above 400 µg N/l). The same is true for the southeastern European rivers that faced a significant fall in 2010 (from above 400 µg N/l to less than 300 µg N/l). On the contrary, concentrations in the northern European rivers are stable and the lowest in Europe (about 40 µg N/l).
The largest proportion of monitoring stations with significant or marginally significant negative trend in total ammonium is found for the western and eastern European rivers, while the lowest proportion is found for the northern European rivers as follows: West: 74.6 % negative, 2.9 % positive; East: 73.5 % negative, 1.9 % positive; Southeast: 70.5 % negative, 3.2 % positive; South: 64.0 % negative, 8.0 % positive; North: 27.0 % negative, 9.8 % positive (sum of significant and marginally significant trends). Countries with more than 60 % of the stations with negative trend in total ammonium are Spain, Latvia, Austria, France, Belgium, Bulgaria, Ireland, Poland, the former Yugoslav Republic of Macedonia, Germany, the United Kingdom, Lithuania and Slovenia.
BOD and total ammonium time series and trends per sea regions (Fig. 4 and Fig. 5)
The largest decrease of BOD from 1992 to 2010 has occurred in the rivers draining to the Mediterranean Sea (78 %), resulting in the lowest concentrations in Europe (about 1.5 mg O2/l) (Fig. 4). Their concentrations fall below stable concentrations in the rivers draining to the Baltic Sea (about 1.8 mg O2/l) with a decrease of 26 %. The second highest decrease of BOD has occurred in the rivers draining to the Black Sea (59 %). Their concentrations (about 2.5 mg O2/l) have approached the concentrations in the rivers draining to the Greater North Sea (about 2.2 mg O2/l) that correspond to the European average. The decrease of BOD is 39 % for the rivers draining to the Greater North Sea and 30 % for the rivers draining to the Celtic Seas, the Bay of Biscay and the Iberian Coast. The concentrations of the rivers draining to the Celtic Seas, the Bay of Biscay and the Iberian Coast have increased compared to 2003 (the lowest level), resulting in the highest concentrations in Europe (about 3.2 mg O2/l).
The trend analysis also shows that the largest proportion of monitoring stations with significant or marginally significant negative trend in BOD is found for the rivers draining to the Mediterranean Sea and the Black Sea, while the lowest proportion is found for the rivers draining to the Celtic Seas, the Bay of Biscay and the Iberian Coast, and the Baltic Sea (Mediterranean Sea: 81.7 % negative, 2.5 % positive; Black Sea: 75.0 % negative, 0.8 % positive; Greater North Sea: 64.2 % negative, 2.9 % positive; Celtic Seas, Bay of Biscay, Iberian Coast: 46.1 % negative, 2.9 % positive; Baltic Sea: 42.8 % negative, 12.3 % positive; sum of significant and marginally significant trends).
The largest decrease of total ammonium from 1992 to 2010 has occurred in the rivers draining to the Mediterranean Sea (78 %) (Fig. 5). The decrease is somewhat lower in the rivers draining to the Black Sea (75 %), the Baltic Sea (74 %) and the Greater North Sea (72 %). The concentrations in the rivers draining to the Celtic Seas, the Bay of Biscay and the Iberian Coast decreased by 60 %. Concentrations in rivers draining to different sea regions have become similar (less than 150 µg N/l for the Mediterranean Sea and the Baltic Sea; less than 200 µg N/l for the Celtic Seas, the Bay of Biscay and the Iberian Coast, and the Black Sea; about 200 µg N/l for the Greater North Sea). The lowest decrease has occurred in the rivers draining to the Arctic Ocean (35 %) with very low concentrations (about 5 µg N/l).
The largest proportion of monitoring stations with significant or marginally significant negative trend in total ammonium is found for the rivers draining to the Celtic Seas, the Bay of Biscay and the Iberian Coast, and the Black Sea, while the lowest proportion is found for the rivers draining to the Arctic Ocean (Celtic Seas, Bay of Biscay, Iberian Coast: 82.6 % negative, 2.8 % positive; Black Sea: 75.5 % negative, 0.9 % positive; Greater North Sea: 67.7 % negative, 3.2 % positive; Mediterranean Sea: 55.2 % negative, 6.9 % positive; Baltic Sea: 55.1 % negative, 5.3 % positive; Arctic Ocean: 23.1 % negative, 15.4 % positive; sum of significant and marginally significant trends).
BOD and total ammonium present concentrations by countries
See WISE interactive maps for information displayed for countries, for river basin districts (BOD) and for individual stations: Mean annual BOD in rivers and Mean annual Total Ammonium in rivers
Countries with more than 50 % of all river stations within the category of the lowest BOD concentrations (class 1: < 1.4 mg O2/l) for 2010 or the latest reported year are France, Latvia, Denmark, Spain, Cyprus and Slovenia. Countries with more than 20 % of the stations within the category of the highest BOD concentrations (class 5: >= 4 mg O2/l) are Romania, Belgium, Hungary, Greece, Albania, Kosovo under UNSCR 1244/99 and Turkey.
Countries with more than 50 % of all river stations within the category of the lowest total ammonium concentrations (class 1: < 0.04 mg N/l) for 2010 or the latest reported year are Croatia, Spain, France, Bosnia and Herzegovina, Liechtenstein, Sweden, Austria, Finland, Norway and Iceland. Countries with more than 20 % of the stations within the category of the highest total ammonium concentrations (class 5: >= 0.4 mg N/l) are Romania, Greece, Luxembourg, Albania, Belgium and Kosovo under UNSCR 1244/99.
This indicator illustrates current biochemical oxygen demand (BOD) and concentrations of total ammonium (NH4) in rivers, and examines trends in both. The key indicator for the oxygenation status of water bodies is BOD, which is the demand for oxygen resulting from organisms in water that consume oxidisable organic matter.
The units used in this indicator are annual average BOD after 5 or 7 days incubation (BOD5/BOD7), expressed in mg O2/l, and annual average total ammonium concentrations expressed in µg N/l.
There are a number of EU directives that aim to improve water quality, and reduce the loads and impacts of organic matter. First, the Water Framework Directive requires the achievement of good ecological status or good ecological potential of rivers across the EU by 2015 and repeals, step-by-step, several older water related directives. Alongside this, the following directives stay in place: the Nitrates Directive (91/676/EEC), aimed at reducing nitrate and organic matter pollution from agricultural land; the Urban Waste Water Treatment Directive (91/271/EEC), aimed at reducing pollution from sewage treatment works and certain industries (see also CSI24 Urban waste water treatment); and the Integrated Pollution Prevention and Control Directive (96/61/EEC), aimed at controlling and preventing the pollution of water by industry.
The UN Sustainable Development Goals also include targets related to river oxygenation conditions. The most relevant targets are 6.3 on improving water quality, specifically addressing wastewater treatment, and 6.6 on protecting and restoring water-related ecosystems, but also 6.1 on safe drinking water and several other targets with a more indirect coupling to organic pollution.
Data source
The data on water quality on rivers in Waterbase are collected annually through the WISE SoE - Water Quality (WISE-6) data collection process. It includes data on nutrients, organic matter, hazardous substances and general physico-chemical parameters, as well as biological data for rivers and lakes. The WISE-6 data flow was new as of 2019, and has from 2020 replaced WISE-4. This reporting obligation is an EIONET core data flow. A request is sent to National Focal Points and National Reference Centres every year with reference to templates to use and guidelines. As of 2015, WISE SoE - Water Quality (WISE-6) supersedes Eurowaternet reporting on river quality (EWN-1).
The data in Waterbase are a sub-sample of national data assembled for the purpose of providing comparable indicators of the pressures, state and impact of waters on a Europe-wide scale. The data sets are not intended for assessing compliance with any European directive or any other legal instrument. Information on the sub-national scales should be sought from other sources.
Monitoring sites selection
Data from all reported monitoring sites are extracted for the indicator assessment. Some data are excluded following the QC process (see QC below). The time series is based on complete time series only (see Inter/extrapolation and consistent time series below).
Determinants
The determinands selected for the indicator and extracted from Waterbase are BOD5, BOD7 and ammonium.
Most countries monitor BOD5. Finland monitors BOD7. Lithuania monitored BOD5 up to 1995 and started monitoring BOD7 in 1996. Latvia monitored BOD7 from 1996 to 2001. Estonia has monitored BOD5 since 2010, replacing BOD7 which was monitored until 2009. 'BOD' is commonly used for BOD5. To be comparable the data of BOD7 have been converted to BOD5 (BOD7=1.16 BOD5).
All countries reported total ammonium until 2006. In 2007, Greece and Liechtenstein started reporting ammonium instead of total ammonium. Instead of total ammonium, Cyprus, Lichtenstein and Slovenia began reporting ammonium in 2008, as did Austria and the Netherlands in 2009, Bulgaria and Latvia in 2010, and Estonia, Norway and Poland in 2011. Besides total ammonium, Slovakia also started to report ammonium for some sites in 2008. Belgium, Germany, Italy, Luxembourg, Slovakia and the United Kingdom report either ammonium or total ammonium for an individual site in a selected year from 2008. Data for either of the two determinands were included in the assessment. For those sites in Slovakia where both were reported, total ammonium data were included in the assessment.
Mean
Annual mean concentrations are used as a basis in the present concentration and indicator analyses. Unless the country reports aggregated data, the aggregation to annual mean concentrations is done by the EEA. Countries are asked to substitute any sample results below the limit of quantification (LOQ) by a value equivalent to half of the LOQ before calculating the site annual mean values. The same principle is applied by the EEA.
The annual data in most cases represent the whole year, but data are used also if they represent shorter periods. Up until 2012, data could be reported at different temporal aggregation levels. Here, annual data have been selected, but if these were not available, seasonal data were selected according to a specific order of preference.
An automatic QC procedure is applied when data are reported, including checking that the values are within a certain range defined for each determinand. Automatic outlier tests based on z-scores are also applied, both to the disaggregated and aggregated data, excluding data failing the tests from further analysis. In addition, a semi-manual procedure is applied, to identify issues which are not identified in the automatic outlier tests. The focus is particularly on suspicious values having a major impact on the country time series and on the most recently reported data. This comprises e.g.:
Such values are removed from the analysis (both time series/trend and present state analysis) and checked with the countries. Depending on the response from the countries, the values are corrected, flagged as outliers or flagged as confirmed valid. Any response affecting the indicator analysis is corrected in the next update of the indicator.
Inter/extrapolation and consistent time series
For time series analyses, only series that are complete after inter/extrapolation (i.e. no missing values in the monitoring site data series) are used. This is to ensure that the aggregated time series are consistent, i.e. including the same monitoring sites throughout the time series. In this way, assessments are based on actual changes in concentration, and not changes in the number of monitoring sites. For the trend analysis, it is essential that the same time period is used for the different monitoring sites, so that the results are comparable. However, the statistical approach chosen can handle gaps in the data series, so inter/extrapolation is not applied here.
Changes in methodology: Monitoring site selection and inter/extrapolation
Until 2006, only complete time series (values for all years from 1992 to 2004) were included in the assessment. However, a large proportion of the monitoring sites were excluded by this criterion. To allow the use of a considerably larger share of the available data, it was decided in 2007 (i.e. when analysing data up until 2005) to include all time series with at least 7 years of data. This was a trade-off between the need for statistical rigidity and the need to include as many data as possible in the assessment. However, the shorter series included might represent different parts of the whole time interval and the overall picture may therefore not be reliable.
In 2009, it was decided to inter/extrapolate all gaps of missing values of 1-2 years for each monitoring site. At the beginning or end of the data series, one missing value was replaced by the first or last value of the original data series, respectively. In the middle of the data series, missing values were replaced by the values next to them for gaps of 2 years and by the average of the two neighboring values for gaps of 1 year.
In 2010, this approach was modified, allowing for gaps of up to three years, both at the ends and in the middle of the data series. At the beginning or end of the data series up to three years of missing values were replaced by the first or last value of the original data series, respectively. In the middle of the data series, missing values were replaced by the values next to them, except for gaps of one year and for the middle year in gaps of three years, where missing values were replaced by the average of the two neighboring values.
In 2018, this approach was slightly modified using linear interpolation for gap filling in the middle of the time series. Moreover, if data were available from 1989-1991 these were applied in the gap filling procedure, making it possible to interpolate instead of extrapolating at the beginning of the time series.
Only time series with no missing years for the whole period from 1992 or 2000 after such inter/extrapolation are included in the assessment. Even if the gap filling is not applied in the trend analyses, the same time series are used, for easier comparison of the time series and trend analysis results. This gap filling procedure increases the number of monitoring sites that can be included in the time series/trend analysis. Using also the shorter time period starting in 2000 allows the inclusion of more monitoring sites, and hence increases the representativeness. Still, the number of monitoring sites in the time series/trend analysis is markedly lower compared to the analysis of the present state, where all available data can be used.
The selected time series (see above) are aggregated to country and European level by averaging across all monitoring sites for each year.
Trend analyses
Trends are analysed by the Mann-Kendall method (Jassby et al., 2020) in the free software R (R Core Team 2020), using the wq package. This is a non-parametric test suggested by Mann (1945) and has been extensively used for environmental time series (Hipel and McLeod, 2005). Mann-Kendall is a test for monotonic trend in a time series y(x), which in this analysis is nutrient concentration (y) as a function of year (x). The test is based on Kendall's rank correlation, which measures the strength of monotonic association between the vectors x and y. In the case of no ties in the x and y variables, Kendall's rank correlation coefficient, tau, may be expressed as tau=S/D where S = sum_{i<j} (sign(x[j]-x[i])*sign(y[j]-y[i])) and D = n(n-1)/2. S is called the score and D, the denominator, is the maximum possible value of S. The p-value of tau is computed by an algorithm given by Best and Gipps (1974). The tests reported here are two-sided (testing for both increasing and decreasing trends). Data series with p-value < 0.05 are reported as significantly increasing or decreasing, while data series with p-value >= 0.05 and <0.10 are reported as marginally increasing or decreasing. The results are summarised by calculating the percentage of monitoring sites within each category relative to all monitoring sites within the specific aggregation (Europe or country). For the relative Sen slope (%), the slope joining each pair of observations is divided by the first of the pair before the overall median is taken and multiplied by 100. Again, this is summarised for Europe or individual countries by averaging across sites. The Sen slope was introduced for this indicator in 2013.
The size of the change is estimated by calculating the Sen slope (or the Theil or Theil-Sen slope) (Theil 1950; Sen 1968) using the R software. The Sen slope is a non-parametric method where the slope m is determined as the median of all slopes (yj−yi)/(xj−xi) when joining all pairs of observations(xi, yi). Here the slope is calculated as the change per year for each monitoring site. This is summarised by calculating the average slope (regardless of the significance of the trend) for all monitoring sites in Europe or a country. The relative change per year (Sen slope %) is calculated as the Sen slope relative to the time series average. Again, this is summarised for Europe or individual countries by averaging across monitoring sites. The Sen slope was introduced for this indicator in 2013.
The Mann-Kendall method or the Sen slope will only reveal monotonic trends, and will not identify changes in the direction of the time series over time. Hence a combination of approaches is used to describe the time series: a visual inspection of the time series, describing whether the general impression is a monotonic trend, no apparent trend, clear shifts in direction of the trend or high variability with no clear direction; an evaluation of significant versus non-significant and decreasing versus increasing monotonic trends using the Mann-Kendall results; an evaluation of the average size of the monotonic trends using the Sen slope results.
For analysis of the present state, average concentrations are calculated across the last 3 years. Outliers and suspicious values are removed before averaging. In this case all monitoring sites can be used, which is a far higher number than those that have complete time series after inter/extrapolation. The 3-year average is used to remove some inter-annual variability. Also, since data are not available for all monitoring sites each year, selecting data from 3 years will give more sites. The average value thus represents 1, 2 or 3 years.
The sites are assigned to different concentration classes and summarised per country (count of sites per concentration class). The classes defining values are based on the range of concentrations found in Waterbase and only give an indication of the relative distribution of values of BOD and ammonium in each country.
The methodology for gap filling is described under inter/extrapolation and consistent time series.
The methodologies used for aggregating and testing trends in concentrations illustrate the overall European trends. Organic and oxygen conditions vary throughout the year, depending especially on flow conditions, affected by weather events etc. Hence, the annual average concentrations should ideally be based on samples collected as often as possible. Using annual averages representing only part of the year introduces some uncertainty, but it also makes it possible to include more river sites, which reduces the uncertainty in spatial coverage. Moreover, the majority of the annual averages represent the whole year.
This indicator is meant to give a representative overview of oxygenation availability in European rivers. This means it should reflect the variability in conditions over space and time. Countries are asked to provide data on rivers according to specified criteria.
The datasets for rivers include almost all countries within the EEA, but the time coverage varies from country to country, both through the analysed period and within the year for which the aggregated mean value is provided. It is assumed that the data from each country represents the variability in space in their country. Likewise, it is assumed that the sampling frequency is sufficiently high to reflect variability in time. In practice, the representativeness will vary between countries.
Each annual update of the indicator is based on the updated set of monitoring sites. This also means that due to changes in the database, including changes in the QC procedure that excludes or re-includes individual sites or samples and retroactive reporting of data for the past periods, which may re-introduce lost time series that were not used in the recent indicator assessments, the derived results of the assessment vary in comparison to previous assessments. As an example, the 2016-2018 assessment of current concentrations of ammonium in rivers is based on 7797 sites, compared to 6577 sites in the assessment of 2015-2017 (i.e. the last year assessment). However, some sites available in the previous assessment are not part of this year’s assessment and vice versa.
Waterbase contains a large amount of data collected throughout many years. Ensuring the quality of the data has always been a high priority. A revision of Waterbase reporting and the database-composition process took place in the period 2016–2018. This included restructuring of the data model and corresponding reporting templates; transformation of the legacy data (i.e. data reported in the past, for the period up to and including 2012); re-definition of specific data fields, such as aggregation period defining the length of aggregation in a year; update of the datasets according to correspondence with national reporters; re-codification of monitoring site codes across Eionet dataflows; and connection of the legacy data time series with the newly-reported data in restructured reporting templates. Still, suspicious values or time series are sometimes detected and the automatic QA/QC routines exclude some of the data. Through the communication with the reporting countries, the quality of the database can be further improved.
Biochemical oxygen demand and total ammonium show oxygen consumption and are thus well suited to illustrating water pollution. However, using annual average values may not fully illustrate the severity of low oxygen conditions.
For references, please go to https://www.eea.europa.eu/data-and-maps/indicators/oxygen-consuming-substances-in-rivers/oxygen-consuming-substances-in-rivers-5 or scan the QR code.
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