Charles A. Ramsey

Representative Sampling for Energetic Compounds at Military Training Ranges

Abstract Field sampling experiments were conducted at various locations on training ranges at three military installations within North America. The areas investigated included an anti-tank range firing point, an anti-tank range impact area, an artillery-range firing point, and an artillery-range impact area. The purpose of this study was to develop practical sampling strategies to reliably estimate mean concentrations of residues from munitions found in surface soil at various types of live-fire training ranges. The ranges studied differ in the types of energetic residues deposited and the mode of deposition. In most cases, the major source zones for these residues are the top two or three centimeters of soil. Multi-increment sampling was used to reduce the variance between field sample replicates and to enhance sample representativeness. Based on these criteria the results indicate that a single or a few discrete samples do not provide representative data for these types of sites. However, samples built from at least 25 increments provided data that was sufficiently representative to allow for the estimation of energetic residue mass loading in surface soils and to characterize the training activity at a given location, thereby addressing two objectives that frequently are common to both environmental and forensic investigations.

A Methodology for Assessing Sample Representativeness

Abstract Assessing sample representativeness is a critical component of any environmental investigation and should be performed before any conclusions are reached. If the samples are not representative, any conclusions or decisions will be incorrect. A complete understanding of the data quality objective process, sample plan design, sample plan implementation, and quality control is required to assess sample representativeness. This article presents a methodology for the evaluation of sample representativeness.

Field Observations of the Persistence of Comp B Explosives Residues in a Salt Marsh Impact Area

Field observations of weathering Comp B (RDX/TNT 60/40) residue were made on a live-fire training range over four years. The Comp B residue was formed by low-order detonations of 120-mm mortar projectiles. Physical changes were the disaggregation of initially solid chunks into masses of smaller diameter pieces and formation of red phototransformation products that washed off with rain or tidal flooding. Disaggregation increased the surface area of the residue, thereby increasing the potential for dissolution. The bulk of the mass of Comp B was in the craters, but solid chunks were scattered asymmetrically up to 30m away.

Measuring Energetic Contaminant Deposition Rates on Snow

Energetic residues from military live-fire training will accumulate on ranges and lead to the contamination of soil and water. Characterizing surface soils for energetic contamination has been conducted extensively in the past. However, deriving mass deposition rates on soils for specific munition-related activities, necessary for determining the cumulative impact of these activities and developing range sustainability models, has been problematic. Factors include determining the energetic residues deposition area, discriminating current deposition from previous activities, separating the residues from the collection matrix, and processing the samples. To circumvent these problems, methods were developed for sampling energetic residues on clean snow surfaces. At firing points, a clean snow surface allows the collection of propellant residues from a known quantity and type of munition. Explosives residues from projectile detonations can be sampled from clean snow- and ice-covered surfaces in active impact areas. Sampling protocols have been optimized and quality assurance procedures have been developed during years of research on munition residues deposition rates. These methods are currently being used in the US, Canada, and Norway for both energetics and metal contaminants with other applications under consideration. This paper describes the current sampling protocol for clean snow surfaces and presents examples of its application.

Comment on “Data Representativeness for Risk Assessment” by Rosemary Mattuck et al., 2005

Following a discussion of the difference between risk assessment for chronic and acute exposures, Mattuck et al. (2005) focus on important factors to consider in sampling designs for chronic exposure decision units. They conclude that, “Probability-based sampling designs are the best for supporting risk assessment because they are unbiased, provide a reliable estimate of variability, and allow statistical inferences to be made from the sample data set” (p. 70). They illustrate the computation of the number of samples required to obtain a reliable estimate of the arithmetic mean concentration and the 95% upper confidence limit (UCL) on the mean. Comments are also offered on the comparative utility of discrete and composite samples. We believe that these issues require further discussion. The equation recommended to compute the number of samples required to estimate a mean contaminant concentration with a specified level of confidence is based on an assumed normal distribution of sample concentrations. However, most data sets representing contaminant concentrations in discrete samples are not normally distributed. For typical low concentrations, there is a natural lower boundary (zero or the detection limit) but no practical upper boundary. Therefore, distributions are often skewed toward higher concentrations. In the absence of an acceptable normalizing transformation, the calculated coefficient of variation (CV) from such data is invalid and can be very large. Table 1 in Mattuck et al. includes sample number estimates based on CVs up to 250%. Such very large CVs are clearly invalid and lead to predictions of sample numbers and UCLs that are both invalid and unrealistic. When discrete sample contaminant concentrations are nonnormally distributed, composite sampling becomes especially attractive because the distribution of composite sample concentrations will often approach normal, in accordance with the Central Limit Theorem. Mattuck et al. acknowledge the benefits of composite sampling to estimate mean concentrations with improved precision and at lower cost. However, they also qualify this by stating, “. . . composites can be problematic when used for statistical tests of parameters that rely on estimates of the sample variance, such as the 95% UCL. . . .” (p. 69). They also claim that “the 95% UCL of the composites may underestimate the true UCL and thus may underestimate risk at the site” (p. 69). First, we must remember that the 95% UCL is a measure of the uncertainty in our estimate of the mean concentration. It is not a prediction of the highest concentration within an exposure area. The objective should be to produce a reliable estimate of the mean and the uncertainty in the mean. Secondly, any estimate of the 95% UCL on the mean, computed using a standard deviation derived from a seriously non-normal distribution, is invalid. In contrast, one derived from replicate composite samples is far more likely to be valid due to better conformance to normality requirements. Mattuck et al. state that, “Data sets with high variability or a small number of samples will have a UCL that may be several times higher than the mean concentration” (p. 66). How can one place any reliance on such an estimate? We believe that an acceptable sampling plan must generate a 95% UCL that is never more than twice the mean concentration estimate, and preferably it should be much closer than that to the mean. Finally, it must be noted that there is no true 95% UCL—it is a probability-based estimate derived from a limited number of samples from a much larger population. These points are illustrated by a typical data set for 2,4dinitrotoluene (2,4-DNT) concentrations in a 10 m × 10 m area at an artillery firing point (Walsh et al., 2005). After dividing the area into 100 equal sized grids, a discrete surface sample (0–2.5 cm) was collected from a random location within each grid. These samples, which ranged from 39 to 82 grams, were analyzed without subsampling. Concentration estimates varied from 0.0007 to 6.4 μg/g. A normal probability plot (Figure 1) was clearly nonlinear, demonstrating that the data was not normally distributed. If we compute the mean and standard deviation despite their lack of validity, we obtain estimates of 1.10 and 1.17 μg/g, respectively (CV = 106%).