All official European Union website addresses are in the europa.eu domain.
See all EU institutions and bodiesDo something for our planet, print this page only if needed. Even a small action can make an enormous difference when millions of people do it!
APPENDIX A: LIST OF DATABASES OR MONITORING PROGRAMMES REVIEWED. LIST OF CONTACT ORGANISATIONS
A1. Introduction
This Appendix discusses some of the following key steps in designing a monitoring programme:
A2. Defining the objectives
The importance of clearly defined, quantitative objectives to the design and implementation of sound, costeffective sampling programmes cannot be overstated. Without careful consideration of the aims of the sampling, the data produced may well be inappropriate, and the number of values generated be either too small or unnecessarily great  with obvious cost penalties in either case. The definition of the objectives has been fully discussed in Section 3.
Previous sections in the report have discussed the questions of (a) what determinants to measure, and (b) how to measure them. For simplicity, therefore, the following discussion is in terms of a discrete sampling programme for one particular chemical contaminant of interest. The same basic principles discussed below apply, however, to all other types of sampling, chemical or biological.
A3. Gaining an understanding of variability
Statistical sampling is primarily concerned with estimating some underlying property of interest (a mean or a 95%ile, perhaps) in an environment of uncertainty. If there were no variability, there would be no need for sampling. Sources of variability involved in measuring the real world can usually be separated into two very distinct types. These are
Variability introduced by the analytical process can fall into either of the above categories. With no extra information about what is being sampled other than the sample values themselves, all the variability appears to be random. However, by adding knowledge, sources of systematic variability can be identified and therefore the random component can be reduced.
The greater the random component of variability, the more samples will be needed to obtain a worthwhile result. That is no more than common sense. The impact of systematic variability, however, is less obvious. A particular systematic cycle that is not taken account of by the sampling programme design can have an effect indistinguishable from random error  and so weaken the effectiveness of the sampling programme. But where knowledge of that systematic cycle is exploited by the programme design  either by sampling at a fixed point in the cycle, or by arranging for the sampling to 'average out' the cyclic effect  the programme can actually be made more effective.
The soundest way of exploring these issues is by conducting a statistical analysis of historical data relating to the water body under investigation (assuming such data are available). This is a valuable preliminary for three main reasons:
A4. Defining the scope of the sampling programme
The scope of the sampling programme is simply the temporal and spatial bounds within which the monitoring will take place, i.e. the sampling population. Ideally this scope would be defined to be the 'target population'. The target population is the collection of all parts of European water resources, temporal and spatial, about which inferences need to be made in order to meet the objectives of the monitoring network. This may be as much as all of Europe's water resources, or it could be a certain part of it defined by the nature of the objectives. For instance, if the objectives require the calculation of the winter mean concentration then the target population would be all water resources sampled during the winter months.
In many situations, however, the scope of the sampling programme will be restricted to a subset of the target population due to practicalities of sampling and costs. This is acceptable if inferences drawn from the sampling population can be reliably extrapolated to the target population. If the sampling population is not an adequate substitute for the target then it is necessary to resolve, or at the very least acknowledge, the conflict between an ideal but impracticable target population, and a convenient but inappropriate sampling scope.
One way of doing this is to change the wording of the objectives so that they take account of the restriction on the target population, enabling future users to judge for themselves the risks involved in extrapolating the results of the sampling programme to other circumstances.
The following examples illustrate the resolution of the scope of the sampling programme.
Objective:
To monitor an effluent discharge to check its compliance with an annual 95th percentile concentration limit.
Target population:
All possible equalsized aliquots that can be drawn from the effluent at very small intervals of time apart (i.e. samples can be taken from any part of the effluent and at any time).
Sampling population:
Could be the same as the target population if there was an automatic sampler (which could be activated at any time of the day or night, any day of the week) drawing from the sole point of discharge.
If sampling was done manually, the sampling population might have to exclude time outside of normal work shifts (nighttime, bank holidays, etc.). This restricted scope would be sufficient if there was no systematic difference between daytime and nighttime concentrations, say.
Alternatively, or in addition, the scope of the sampling programme would be a restricted subset of the target population if there were several discharge points, but sampling could only be done at one of them. The sampling population would be adequate if there were no differences between effluent quality from point to point.
Objective:
To estimate the difference between annual mean concentrations of a particular pollutant in a receiving water upstream and downstream of the discharge.
Target population:
There are two parts to the target population. the first is all possible equalsized volumes of water that can be drawn from the receiving body at very small intervals of time apart, from any depth and any site in the water providing that it is upstream of the discharge and does not contain any part of the effluent. The second is the same as the first with the exception that the possible sampling sites must be downstream of the discharge and not influenced by other discharges or sources of pollutant.
Sampling population:
In addition to the possibility of temporal restrictions such as those outlined in the first example, the scope of the sampling may be limited by other factors. For instance, it may not be possible to establish whether or not a particular upstream sampling site is free of the effluent being monitored as it may depend on stream flow rates and mixing patterns etc. In such a situation, the upstream sampling population might be restricted to sites more than a certain distance upstream of the discharge but downstream of any other sources of pollutant. Results from this sampling population are very likely to be reliably extrapolated to the target population.
A5. Compliance testing/threshold excedence
Most European compliance testing is of the 'exceeding the threshold' variety, i.e. no more than 'x' excesses out of 'n' tested samples. In this case if information is reported as 'pass' or 'fail' against a level or standard then common numbers of samples are needed for fair comparisons.
A6. Percentile estimation and estimation of averages
If all the data used in calculating each statistic, or just the statistic and some estimate of variance (e.g. standard deviation), are provided then it is possible to judge the quality of the estimates and determine how significantly different they are from each other. Having a common sampling frequency for a determinant would not ensure the estimates produced in different areas would have the same quality, or even a minimum quality, because of the differences in variability from area to area.
A better approach would be to specify a minimum level of precision and confidence to which the estimates must conform (i.e. a minimum estimate of quality). The minimum number of samples required to achieve this precision and confidence can then be calculated for each site or area. The following subsection defines what is meant by precision and confidence and the subsection after that describes how this can be used to determine the minimum number of samples.
A6.1 Precision and confidence
The reason for designing a sampling programme in the first place is because it is not possible to sample the whole of the target population. Therefore, the values obtained for the statistical objectives are estimated from a (usually) much smaller subpopulation of samples and are, consequently, subject to a certain amount of error or uncertainty. Choosing the precision and confidence sets limits on how much of this uncertainty can be tolerated in the results of the programme.
Consider some quantity that has been estimated from the sampled data. This estimate will almost always differ from the true value (i.e. the quantity which would be calculated if the whole of the target population was sampled). Answering the following two questions will define the precision and confidence.
Confidence is expressed as a percentage, so for example, a confidence of 99% means that if the sampling programme could be repeated 100 times, the answer would be within the precision tolerance on 99 occasions.
A6.2 Determining the number of samples
Once the precision and confidence have been set and some estimate of the random variability of the samples is known (based on previous monitoring results), then the minimum sampling frequency can be derived.
By way of a simple example, suppose that the intention is to estimate the mean of some determinant over a year. The standard formula for calculating the required number of samples (assuming that the random variability of the samples can be modelled by a Normal distribution) is:
where
n is the minimum number of samples needed,
d is the desired precision,
u is a factor related to the desired confidence (obtained from the percentiles of the standard Normal distribution), and,
s is a reliable estimate of the variability (expressed as the standard deviation).
[If the desired confidence is C%, then the factor u is the (100+C)/2th percentile of the standard Normal distribution. For example, if C is 95 then u is 1.96 (the 97.5th percentile).]
\tab \tab
Table A.1 below shows the effects of different confidences and precisions on the numbers of samples needed. The table combines the desired precision and the random variability by using the relative precision (the ratio of precision to standard deviation).
Table A.1 Minimum numbers of samples needed to obtain certain precisions and confidences.
Confidence, C 

Relative precision, d/s 
90% 
95% 
99% 
99.9% 
0.1 
273 
385 
666 
1083 
0.2 
68 
96 
167 
271 
0.3 
31 
43 
74 
121 
0.4 
17 
24 
42 
68 
0.5 
11 
16 
27 
44 
0.6 
8 
11 
19 
30 
0.8 
5 
6 
11 
17 
1.0 
3 
4 
7 
11 
This example relates to the simplest statistical objective, i.e. estimating a mean. However, the same principle applies to more complicated statistical objectives (e.g. the median, 10th percentile geometric mean, etc.).
A7. Potential impact on current monitoring practice
To gain some understanding of the levels of sampling ideally required for an EEA network some estimate of variance is required for each determinant. These can best be drawn from current monitoring practices. To take the example of river nutrients a key determinant is soluble reactive phosphorus (SRP). The National Rivers Authority of England and Wales has an extensive network of sites which will monitor for SRP in its proposed general quality assessment scheme (GQA). To obtain an average estimate of variance all means and standard deviations were calculated for all of the 5,000 sites sampled more than 12 times over the three years between 19901992.
As riverine orthophosphate levels follow a highly skewed distribution (approximately lognormal) the values of the site standard deviations are spread across a large range (4 orders of magnitude). A log transformation of the sample values before calculating the standard deviations reduces the spread of these standard deviations to one order of magnitude. The advantage of this technique is that the spread of precisions obtained for each site will be correspondingly small allowing a better overall assessment of the number of samples required. The average estimate of standard deviation for the log_{e} transformed data was calculated to be 0.74. This estimate of variability can now be applied to assess the number of samples required to meet a particular precision.
The classification used in the Dobrí\'9a Assessment (1995) has six classes with boundaries for orthophosphate at 25, 50, 125, 250 and 500 \'b5g/l of PO_{4}P. The lowest of these classes represents a site with no anthropogenic input and the highest class indicates a site with high levels of nutrient input either through agricultural runoff or sewage input. We can specify the desired precision and confidence in terms of the width of the classes. For example, we may wish to be 90% confident that a site reported as class B is really class B (i.e. its true geometric mean SRP lies between 25 and 50 m g/l) when its geometric mean SRP is more than 25% of the class width away from the class boundaries. To achieve this we need to take enough samples at the site; the minimum number of samples required is given by the equation in the previous section, i.e.
where 0.74 is the average standard deviation of log_{e} SRP and 0.173 is the precision (one quarter of the typical class width on a log scale). This formula can be rearranged to estimate confidence intervals associated with particular sampling frequencies. Table A.2 below presents widths of confidence intervals based on log transformed orthophosphate data.
Table A.2 Widths of confidence intervals based on log transformed SRP data from the National Rivers Authority of England and Wales GQA database
Number of samples 
Mean of samples 
relative lower 90% 
relative upper 90% 
6 
0.61 
1.65 

12 
0.70 
1.43 

18 
0.75 
1.34 
Note: This is to gain the required precision at each site. A different number would be required for regional or larger scale aggregation of data.
For example, if the mean orthophosphate concentration of a site sampled 12 times was 100 \'b5g/l we could say with 90% confidence that the value lies between 70\'b5g/l and 143 \'b5g/l. This precision may well be expectable. Few monitoring programs sample their sites at an intensity of 50 times per year. There are several options:
For interregional comparisons, the number of sites per region needs to be specified having first specified the number of samples per site. If, by way of example, we take the whole area of the National Rivers Authority of England and Wales to be one region (or strata, see Section 6) then we can estimate the number of sites required using the formula given in Section 6.3. The intraregion (intrastratum) standard deviation of site geometric means is 1.62. If we wanted a precision of one half of the class width and a confidence of 90% for interregional comparisons, then the required number of sites is
A8. Determining when and how often to sample
Having determined how many samples should be taken, the next task is to decide on the duration of the sampling programme, and how to spread the samples over that total sampling period. In other words, once the question 'How many?' has been answered, the questions 'How often?' and 'When?' then need to be addressed.
A8.1 Defining the timescale
Many objectives  especially those relating to compliance assessment  have a predetermined duration. For other types of enquiry a period of 12 months is often convenient (though the traditional idea of an annual statement of quality should not be perpetuated merely by default).
Where the choice is more open, it is ultimately a matter of weighing up the extra costs of carrying out the sampling over a shorter time period against the benefits of obtaining the results that much sooner.
A8.2 Allocating the sample times
The main issue here is whether to allocate the samples at random, or whether to spread them systematically (through time, or by volume, or some combination of these, according to the identified target population). The choice depends very much upon (a) the objective, and (b) what is known about the variability of the system. The principal advantage of random sampling is that it is statistically foolproof  a particular advantage when little can be assumed about the system being sampled. (It is also an essential component of any regulatory sampling programme, incidentally, as it is the only way of retaining the element of surprise.)
Strict random sampling does, however, pose severe organisational difficulties Moreover, it does not guarantee that the results from any one sampling programme will be particularly representative. For these reasons, systematic sampling will often be a preferable alternative. With such a regime, however, it is important to be sure that the sample times and dates do not unwittingly move in step with some important cycle in the physical system  unless, of course, it is intended to exclude this from the target population. For example:
A9. Timebased and volumebased sampling
There are two fundamentally different ways in which we can visualise quality variations in a river:
If flow was constant through time the two representations would be identical. Otherwise, the volume based description can be thought of as being a 'distorted' timebased version in which the clock is driven by a waterwheel rather than by clockwork.
Virtually all routine water quality monitoring is timebased rather than volumebased. For example, the sampling regime for a river will be expressed as 'sample once a fortnight' rather than 'sample once every 4000 MI'. As most of the EEA's objectives relate to concentrations, the timebased description is the correct one to use.
When the primary interest is in, say, mean loads, there is an inherent disadvantage with timebased sampling: a straightforward mean concentration will in general lead to a biased estimate of load. As high flows occur for a relatively short time, very few will happen to coincide with the sampling occasions. (There might also, indeed, be a deliberate policy of avoiding sampling on occasions of very high flow for safety reasons.) The resulting concentration versus flow plot will therefore have a great preponderance of lowflow points. As a consequence, evidence for a significant association will always hinge unsatisfactorily on at most a handful of highflow samples. With sample sizes of only 30 or 40, moreover, there is a real risk that high flows are entirely underrepresented. The danger then is that the sample variability badly underestimates the true variability in the underlying population, and so leads to unrealistically optimistic statements of precision (Ellis, 1989).
With a volumebased approach, in contrast, sampling frequency will automatically be stepped up in periods of relatively high flow (as, for example, with flowproportional sampling devices), and so the mean concentration at the end of the year provides a direct estimate of mean load.
The report on current EEA surface water quality monitoring networks (Kristensen and Bøgestrand 1996) identifies 19 sampling programmes which are specifically designed to assess contaminant loads in river systems across Europe. The report indicates that without exception these programmes all have time rather than volume driven sampling regimes.
Calculation of loads can be addressed in two ways using an annual average flow to produce a simple arithmetic mean of load or use the instantaneous flow associated with each sample to produce a flowweighted average. Both of these approaches have their associated pitfalls when compared to flow driven sampling regimes.
Walling and Webb (1985) used a twoyear sequence of hourly suspended sediments data from a sampling station on the River Exe, together with corresponding hourly flows provided by South West Water. Using this virtually continuous record, they were able to mimic the results of weekly, fortnightly and monthly sampling programmes and hence demonstrate for any particular load estimation formula (i) its average bias, and (ii) the relationship between precision and number of samples. For the full data set there was a positive underlying association between concentration and flow, and this resulted in load estimates based on the simple arithmetic mean approach to underestimate the true value. In this instance, the estimates from weekly and fortnightly programmes were on average only 38% of the true load, whilst for the monthly programmes the ratio dropped still further to 25%. In contrast, the flowweighting approach showed negligible bias.
The lack of bias, though desirable, is not everything, and the simulation results also clearly highlighted the greater imprecision necessarily introduced by flowweighting when there is a positive association between concentration and flow. In other words, errors from repeated use of the flowweighted approach will average out in the long run, but the estimate in any one application may be a long way from the true figure.
The Helsinki Commission which is responsible for the Convention on the Protection of the Marine Environment of the Baltic Sea Area provides the only identified example of a flow driven sampling program. The approach taken by the commission to produce reliable data includes pollution load compilations (PLC's) from landbased sources. The associated sampling strategy is aimed at providing precise estimates of input load and has three components:
Experience has shown the positive correlation between periods of high river flow and high load input, especially for heavy metals, suspended solids and nutrients. For all rivers a minimum of 12 data sets are collected throughout the year, the data does not have to be collected at regular monthly intervals but at a frequency which appropriately reflects the expected river pattern, measurements should, therefore, cover low, mean and high flow data to gain a more representative assessment of contaminant load.
The benefits of flow related sampling are clear to see. These have to be carefully weighed against the increased cost and logistical consideration of adapting this approach to met the Agency's needs.
For references, please go to https://www.eea.europa.eu/publications/9291670235/page021.html or scan the QR code.
PDF generated on 08 Nov 2024, 05:11 PM
Engineered by: EEA Web Team
Software updated on 26 September 2023 08:13 from version 23.8.18
Software version: EEA Plone KGS 23.9.14
Document Actions
Share with others