Passive Sampling of Munitions Constituents

From Enviro Wiki
Jump to: navigation, search

Passive sampling using integrative samplers enables the monitoring of munitions constituents in underwater environments over timescales of days to months and at ultra-low concentrations. Munitions compounds have an affinity for some resins and polymers that, when submerged for a period of time and corrected for the environment-specific sampling rate, can be used to determine time weighted average ambient water concentrations. This article primarily details the Polar Organic Chemical Integrative Sampler (POCIS), its optimization using laboratory flume and field experiments, and its application at munitions-impacted underwater sites.

Related Article(s):

Munitions Constituents - Soil Sampling

CONTRIBUTOR(S): Dr. Guilherme Lotufo and Gunther Rosen

Key Resource(s):


Figure 1. Underwater munitions are derived from UXO and historical disposal practices
Figure 2. Conceptual diagram of MC release from a breached underwater UXO.

Underwater unexploded ordnance (UXO) at active and former training ranges and discarded military munitions (DMM), collectively referred to as underwater munitions and explosives of concern (MEC), present challenges due to both immediate safety considerations (e.g. explosive blast) and potential ecological and human health impacts resulting from the release of munition constituents (MC) to the marine environment. Underwater sites around the world are known to contain MEC as a result of military activities or historic disposal events (Figure 1). MC including 2,4,6-trinitrotoluene (TNT) and 1,3,5-trinitro-1,3,5-triazine (RDX) may be released into the surrounding aquatic environments as a result of MEC corrosion and breaching of the munition’s outer casing[2][3][4][5][6][7][8][9]. Release may also occur from fragments of explosives formulations that become exposed following low-order (incomplete) detonations (LOD) resulting in fully breached munitions[9] (Figure 2).

The rate of release of MC from MEC into the surrounding environment is expected to be influenced by the size of the initial breach and growth of the breach hole in the munition casing, the radius of the cavity formed due to loss of MC mass from inside the MEC, the dissolution rate from solid to aqueous phases of the MC inside the MEC, the outside ambient current to which the casing breach hole is exposed, and the mass of MC remaining inside[4][10]. Subsequent to the breaching event, concentrations in the surrounding environment are expected to fluctuate over time because of the dependence of release kinetics on the above parameters, as well as hydrodynamic conditions leading to dilution effects, sorption to suspended particles, photo-transformation, and other factors leading to MC loss from the aquatic environment[6][11][12]. As a result of slow release and rapid removal of MC in the surrounding water[8][11][12], MC have been detected at low frequency relative to the number of samples examined and at low concentrations at Underwater Military Munitions (UWMM) sites[6][8][11]. Overall, munitions constituent persistence in the environment is a key determinant of exposure[11]. Exposure to MC in water has been shown to be toxic to aquatic organisms belonging to various taxonomic groups[8][11][13][14].

Underwater Sampling Challenges

Considering that MC are expected to be present at UWMM sites mainly at ultra-low concentrations and with concentrations decreasing with increasing distance from the source of released MC[7][15][16][1], a number of challenges prevent accurate assessment of environmental exposure using traditional water, sediment, and tissue sampling and analyses. These challenges include a high level of effort or difficulty required to:
     1. identify breached underwater MEC that are actually releasing MC;
     2. measure MC in the water column at low levels; and
     3. characterize water column exposure using the appropriate spatial and temporal scales for determining ecological risk.

Standard environmental sampling, such as grab sampling of surface water, only generates information for the time of sample collection, and spot grab sampling strategies may inadequately capture temporal changes[17] in MC concentrations that occur at UWMM sites, thereby providing an inaccurate measure of environmental exposure. In contrast, integrative passive sampling has been used to derive ultra-low and time-weighted water concentrations for a wide range of environmental contaminants[18], including MC[7][19][20][21][22][23]. Polar organic chemical integrative samplers (POCIS)[24] currently are the most widely used samplers for weakly hydrophobic contaminants (typically those with log Kow < 4).

The US Department of Defense’s Environmental Security Technology Certification Program (ESTCP) provided funding for research aimed at optimizing use of POCIS passive sampling technology for sampling MC in water and at demonstrating the application of POCIS to determine time-weighted average (TWA) water-column concentrations in the vicinity of MEC at a UWMM site (ESTCP Project ER‐201433)[1]. Some results of that project are presented in the following sections of this article.

Technology Overview

Figure 3. the structure of a POCIS where stainless steel encompasses the PES membranes and the adsorbent in the middle (from Morin et al. 2012 and Seethapathy et al. 2008)[25][26].

The POCIS consists of a receiving phase (sorbent) sandwiched between two polyethersulfone (PES) microporous membranes with ~0.1 μm pore size[24] (Figure 3). The sampler is held together by two stainless steel rings with an interior diameter of 51-54 mm, which provides an exposure surface area of 41-46 cm2. The POCIS are available commercially from Environmental Sampling Technologies (EST; St. Joseph, Missouri), and contain the widely used Oasis® hydrophilic-lipophilic balance (HLB) polymer as the sorbent. A variety of sampler holders and canisters have been used to protect the passive samplers in the field. The holder and canister shown in Figure 4 are commercially available from EST.

Figure 4. Sample holder (left) and protective canister for multiple POCIS (right, both supplied by EST).

For passive sampling of contaminants, the POCIS are kept immersed in water typically for two weeks to one month. However, depending on the study objectives, deployment times can range from days to months. At the end of the deployment time the POCIS are collected and transported to a laboratory where they are dismantled for collection of the full mass of sorbent. Analytes are extracted from sorbent using standard techniques, typically by organic solvent extraction in a chromatography column. The eluate can be analyzed using instrumental techniques such as liquid chromatography coupled with mass spectrometry (LC/MS) or by gas chromatography coupled with MS (GC/MS). More than 300 chemicals with a wide range of commercial and industrial applications have been detected or quantified by the POCIS in laboratory and field testing[25].

Accumulation in the POCIS is based on passive diffusion of analytes from water into the POCIS receiving phase. The POCIS is designed to operate as an infinite sink for analytes during the linear uptake stage. As such, it is used to determine TWA concentrations but does not capture any fluctuations in concentrations that occur during the deployment period. In order to obtain TWA concentrations of the molecules being studied, laboratory or in situ calibration of the POCIS is necessary. The calibration allows the determination of chemical-specific sampling rates (Rs) using experimentally derived uptake rates. The Rs is defined as the volume of water cleared in a unit of time (typically L/d). The sampling rates are necessary to convert the mass of a compound accumulated in the sorbent phase of the sampler to its concentration in the environmental medium sampled. Sampling rates are typically empirically derived during laboratory studies employing a closed system in which the contaminants of concern are spiked only at the beginning of the experiment or at constant time intervals[19][27][28]. The POCIS-derived TWA is calculated using Equation 1:

Equation 1:     Cw =  N / (Rs * t)
Cw is the TWA water concentration (ng/L),
N is the mass of the chemical accumulated by the sampler (ng),
Rs is the sampling rate (L/day), and
t is the exposure time (days).

A multitude of factors affect the sampling rate. The pattern and rate of water flow (i.e., current’s velocity and direction) across the PES membranes that house the POCIS sorbent generally have the largest impact on Rs. This is because diffusion of dissolved substances across the membrane is dependent on the thickness of the water boundary layer at the membrane surface, which is affected by water flow induced turbulence around the sampler[29][30]. Other variables such as biofouling have also been found to have some impact on Rs[31]. The accuracy of calibrated sampling rates for subsequent environmental studies is dependent on how similar the site exposure conditions are to those used in the calibration experiment[29]. Therefore, samplers should be calibrated in conditions as close as possible to those expected at the monitored sites[23].

Because of the wide range of field environmental conditions, the biggest challenge facing the use of POCIS has been the lack of a correction method to quantify the effect on the uptake process when field conditions vary from those of the calibration experiment. To overcome this issue, performance reference compounds (PRCs) with experimentally quantified dissipation rates can be spiked into the samplers prior to deployment to account for the effects of field exposure conditions on RS values. PRCs should be chosen that do not occur in the environment in which the sampler will be used. The selected PRC should also be significantly but not completely depleted over the planned deployment period. The mass of PRC lost during deployment is then used to improve the accuracy of the estimated TWA concentration of the analyte of interest. Performance reference compounds have been successfully and widely used to correct for the impact of exposure conditions on hydrophobic passive samplers[32]. A study by Li et al.[31] was the first to demonstrate the reliable use of PRCs for determining TWA concentrations in the field using POCIS.

POCIS typically exhibit negligible analyte loss rates even when local environmental concentrations of the analyte drop to undetectable levels for some portion of the deployment period. This allows small masses of a chemical of interest from episodic release events to be retained in the device at the end of the deployment period[19][33][34][35]. Therefore, the POCIS offer an advantageous alternative to traditional sampling methods (e.g. collection of discrete grab samples) at sites where fluctuation in concentrations or low-level concentrations are expected to occur, such as in the vicinity of underwater munitions. The continuous sampling approach of POCIS allows quantification of concentrations in an integrative manner as time weighted averages that are representative of the entire sampling period. The cumulative sampling of contaminant mass over the sampling period also enriches the analyte in the sorbent, which improves detection and quantification of the analyte. As another advantage, the POCIS provides protection of sorbed analytes against decomposition during post-deployment transport and storage[36].

Optimization of POCIS for Munitions Constituents

Figure 5. Flume setup for optimization of POCIS and determination of MC sampling rates.
Figure 6. Experimental determination of MC release rate from a perforated munition in a large flume.

The POCIS has recently been demonstrated to be effective for assessment of environmental exposure of MC[7][1][19][20][21][22][23][37]. At experimental concentrations of 1 μg/L, TNT, aminodinitrotoluenes (ADNTs), and RDX accumulated in the POCIS at a linear rate for at least 14 days, with sampling rates between 34 and 215 mL/day[19]. Calibrations were also performed for dinitrotoluenes (DNTs)[21]. Laboratory tank experiments have demonstrated that POCIS can integratively sample water concentrations of MC under widely fluctuating environmental concentrations[19].

As flow rate can have a significant impact on sampling rate, calibration across a range of flow velocities was conducted using MC spiked into a large flume located at the U.S. Army Corps Engineer Research and Development Center (ERDC) in Vicksburg, MS (Figure 5), where flow velocities were precisely controlled[21]. The flume water (60,000 L) was spiked at 1 μg/L for multiple MC, and POCIS were exposed for 10 days at each of three flow velocities (7, 15, and 30 cm/s). The flume water was drained, refilled, and re-spiked between experiments. Discrete (grab) samples were collected from the flume every other day for the calculation of Rs under each flow velocity. Sampling rates for TNT varied by up to a factor of two among the three velocities and increased as flow velocity increased. However, the sampling rate for RDX was minimally influenced by flow velocity. The data has been used to derive velocity-specific Rs for UWMM sites, as detailed below.

A follow-up flume study investigated the release of TNT and RDX from Composition B fragments under two realistic exposure scenarios with flow set at 15 cm/s. The first represented the release of MC from fully exposed Composition B, and the second represented release through a small hole, simulating a breached munition (Figure 6)[22]. Release of MC through a small hole was approximately 10 times lower than from fully exposed Composition B, demonstrating the strong influence of exposure to flow on release rates. MC in the flume water was quantified using frequent grab sampling and POCIS. For TNT, POCIS estimated time-weighted-average concentrations were up to 40% higher than those derived from grab samples, while for RDX differences were 6% or less, demonstrating that POCIS provide reliable temporal integration of changing environmental concentrations for common MC.

For the laboratory studies described above, grab samples (1 L) were analyzed by solid phase extraction (SPE) using Oasis HLB SPE columns, eluted with ethyl acetate, and brought to a final volume of 0.5 ml using procedures optimized by Belden et al.[19]. The POCIS were disassembled, and the sorbent was rinsed into empty SPE tubes. MCs were eluted with ethyl acetate and brought to a final volume of 0.5 ml. All extracts were analyzed using an Agilent 6850 GC coupled with a 5975C mass selective detector (MSD) using negative chemical ionization with three ions selected for ion monitoring for each analyte. Internal calibration was performed using 13C-TNT[19].

Controlled Field Demonstration

Figure 7. Controlled field demonstration site, Santa Rosa Sound, Florida
Figure 8. 15g of composition B (left) placed in mesh bag (right) as used in the controlled field demonstration.
Figure 9. Location of POCIS surrounding Composition B source during controlled field demonstration.
Figure 10. POCIS-determined MC concentrations from the controlled field demonstration.
Figure 11. Biofouling did not affect POCIS uptake of TNT or RDX [7].

The POCIS were evaluated for their ability to detect releases at low parts per trillion concentrations in a positive control field study using a known mass of Composition B fragments deployed in an estuarine embayment similar to sites that contain UXO or DMM[7]. This first known field demonstration of the POCIS for MC was conducted in 2014 adjacent to the U.S. Environmental Protection Agency’s (USEPA) Gulf Ecology Division at Santa Rosa Sound, Florida (Figure 7). This site was chosen because it exhibits physical characteristics similar to other underwater sites with MC present (i.e., sandy substrate, estuarine/marine water, and subtropical temperatures). POCIS were also deployed at the site prior to the positive control study, and the results indicated the absence of detectable background MCs. Placement of 15 g of Composition B (RDX and TNT) fragments in a mesh bag inside a POCIS canister (Figure 8) suspended just above the sea floor simulated explosive fill material semi-encapsulated inside a munition. For each of 20 sampling locations, three POCIS were placed inside field canisters and deployed for a 13-day period at varying distances, directions, and depths from the “source” canister containing Composition B (Figure 9). POCIS-derived TWA water concentrations for TNT and RDX were low (11–218 ng/L) and decreased with distance from the source (Figure 10), as expected considering the small mass used for the study and the slow dissolution rate of Composition B in water[38]. Both TNT and RDX were below quantitation limits (5 - 7 ng/L) 5 m from the source. All grab water samples were below method detection limits (120 and 50 ng/L for RDX and TNT, respectively).

Moderate biofouling of POCIS membranes after 13 days led to a subsequent experiment to quantify potential effects of biofouling on the sampling rate for munitions constituents. After biofouling was allowed to occur at the field site, POCIS were transferred to aquaria spiked with munitions constituents (Figure 11). No significant differences in sorbent uptake rates of TNT or RDX due to biofouling were observed over a range of biofouling intensities[7].

Monitoring MC Using Passive Samplers at Underwater Munitions Sites

A POCIS demonstration was conducted in early 2016 at Bahia Salina del Sur (BSS), a former Naval Training Range in Vieques, Puerto Rico, with support provided by Naval Facilities Engineering Command and a multitude of stakeholders, to achieve the following goals:

1. A reconnaissance survey by dive qualified UXO technicians within one month prior to POCIS study to identify candidate munitions;
2. Deployment of POCIS for three weeks;
3. Comparison of POCIS with grab water results; and
4. Comparison of detected MC with ecological risk thresholds.

Following a successful reconnaissance survey that identified more than 25 items of varying type, condition, position, and substrate, UXO and scientific dive teams selected 15 MEC that the project team thought had the highest potential to be actively leaking. The MEC locations are shown in Figure 12. After sweeping the area with a magnetometer, samplers mounted to a weighted concrete block system were placed approximately 15 cm away from the MEC (Figure 13). Placement was on sand or hard bottom, but never on top of coral colonies or ecologically important species or habitat. Target items included an assortment of projectiles, old style and MK 80 series GP bombs varying in condition and size, ranging from minimally corroded, apparently intact items to obviously breached items. Some of the items were clearly breached by corrosion over time, while others were the result of low order detonations. When feasible, the samplers were placed in close proximity (e.g., 15 cm) to visible breaches. Samplers were recovered for analysis 19-21 days later.

Figure 12. Stations (15 in total) in Bahia Salina del sur where POCIS were deployed.
Figure 13. POCIS sampler with weighted anchor system adjacent to the base of a 500 pound "Old Style" General purpose bomb.

Discrete (grab) water samples (1 L) were collected within 30 cm of the POCIS sampler at all stations by the scientific dive team during both the deployment and the recovery effort. Water samples were extracted by the project team on site for preservation and safe shipment to the analytical laboratory. An acoustic Doppler current profiler (Nortek Aquadopp, Nortek USA, Boston, MA, USA) was deployed at multiple locations within and outside the BSS, during both deployment and recovery operations, to obtain current velocity and direction data at or near sampler locations. The current velocity data were used to derive TWA water concentrations from POCIS using corrections based on flow rate from the flume studies described above. The POCIS-derived time weighted average water concentrations were calculated using Equation 1. Flow-corrected sampling rates were generated for each MC analyzed based on mean flow velocities and using Rs obtained in calibration experiments under different flow conditions[1].

Water concentration results for TNT and RDX are summarized in Table 1. The frequency of RDX detections was a factor of 4 (or more) higher for POCIS as compared to grab samples, potentially due in part to lower quantitation limits for the POCIS samplers (Table 1). RDX exposure also may have been episodic in that RDX was detected in three grab samples collected during the installation of the POCIS at the beginning of the deployment phase, while none was detected in grab samples collected during the recovery of the samplers.

Measurable concentrations of TNT and measurable but much lower concentrations (< 500 ng/L) of other nitroaromatic MC (i.e., 1,3,5-trinitrobenzene, 4-aminodinitrotoluene and 2,4-dinitrotoluene) were identified in both POCIS and grab samples from one of the 15 sample points (designated Station T14) located near a 1,000 lb GP bomb with visible small breaches (Table 2). The relative similarity between the TNT concentrations in two grab samples taken 3 weeks apart (4,470 and 7,479 ng/L), and the similarity between POCIS derived concentrations and average grab sample concentrations of TNT (11% higher than POCIS), suggests that the breaches may have functioned as a continuous source of contaminant mass in the immediate vicinity of the sample point. These concentrations are similar to previously reported concentrations of TNT (7,900 and 17,700 ng/L) in water sampled 1 m from a breached GP bomb[39]. TNT was not detected at concentrations above the quantitation limit in either type of samples collected from the other sample points (Table 1). Concentrations of other MC constituents in grab samples collected at Station T14 were also similar to the POCIS results (Table 2). The similarity of MC concentrations in grab samples to those determined by analysis of the POCIS demonstrates that the POCIS provides reliable temporal integration of varying environmental concentrations of MC released from breached MEC at UWMM sites.

Table 1. Summary of TNT and RDX analytical data from POCIS and grab samples collected at Bahia Salina del Sur in January 2016[1].


Detection Limit
POCIS TNT 14 1 7 5,304 3.7 11.1
RDX 14 11 79 5.0 - 12.6 2.9 8.8
Grab (Initial) TNT 15 1 7 4,470 8.4 25
RDX 15 3 20 24 - 51 18 54
Grab (Final) TNT 15 1 7 7,497 8.4 25
RDX 15 0 0 -- 18 54
Note: One POCIS sample was lost during extraction in the laboratory.
Table 2. Comparison of MC concentrations in POCIS and grab samples collected near MEC at Bahia Salina del Sur [1].
Compound Station POCIS
Grab Samples (ng/L) POCIS /
Initial Final Average
TNT T14 5,304 4,470 7,479 5,975 0.9
TNB T14 <1.9 22 35 29 --
2,4-DNT T14 46 13 17 15 3.1
4-ADNT T14 103 19 73 46 2.2
2-ADNT T14 54 31 89 60 0.9
DNANIL T14 6 <12 <12 -- --
RDX T8 13 <18 <18 -- --
RDX T9 11 <18 <18 -- --
RDX T10 12 26 <18 17.5 0.7
RDX T11 7 24 <18 16.5 0.4
Note: Non-detects expressed as <Method Detection Limit (MDL).

Related Study: Monitoring MC Using Passive Samplers in Swiss Lakes Near Munitions Dumping Sites

Another recent study has also investigated the use of integrative samplers (POCIS and other technologies) to monitor MC in the water column at field sites. Estoppey et al.[23] conducted calibration studies using POCIS and the polar version of the Chemcatcher[40] in a channel system supplied with continuously refreshed lake water spiked with 9 different MC. Exposure parameters were kept as close as possible to those expected at the study site located at the bottom of two Swiss Lakes where tons of ammunition waste were dumped between 1920 and 1967. Estoppey et al. [23] demonstrated that analysis of the PES membrane that houses the HLB sorbent is highly important, especially for more hydrophobic MC such as nitroaromatics, as uptake in the PES was substantial, thus delaying the transfer of these compounds to the sorbent. They suggested using a larger pore size for the PES membrane or using a nylon membrane. Estoppey et al.[23] emphasized the benefit of correcting for flow velocity and recommended concurrent exposure of low-density polyethylene strips loaded with PRCs during POCIS calibration so that mass-transfer coefficients at the water boundary layer (kw) could be determined from PRC dissipation, then used to measure flow rates in the field. Integrative TWA concentrations of explosives measured in the lakes were similar for POCIS and Chemcatcher and confirmed results obtained by previous studies based on grab sampling. TWA concentrations were about 0.4 ng/L for RDX and HMX and 0.1 ng/L for pentaerythritol tetranitrate (PETN) at the bottom of Lake Lucerne (approximately 200 m below surface). At a similar depth in Lake Thun, TWA concentrations of HMX, RDX, and PETN were lower and most of the time below quantitation limits (0.02 – 0.3 ng/L). In both lakes, nitroaromatic concentrations were below quantitation limits (0.02 – 10 ng/L).

Emerging Technology

Ethylene-vinyl acetate (EVA) passive samplers also show promise for quantifying MC in the water column[41]. The potential advantages of EVA are that the target compounds come directly into contact with the thermoplastic material that has both hydrophobic and hydrophilic components, eliminating the need for a membrane and with it any potential effects on flow or contaminant interception. The ratio of vinyl acetate to ethene in the polymer of the sampler can also be manipulated to adsorb specific target chemical types.


  1. ^ 1.0 1.1 1.2 1.3 1.4 1.5 1.6 Rosen, G., Colvin, M., George, R., Lotufu, G., Woodley, C., Smith, D. and Belden, J., 2017. Validation of passive sampling devices for monitoring of munitions constituents in underwater environments (No. SPAWAR-SCP-TR-3076). SPAWAR Systems Center Pacific San Diego. Report.pdf
  2. ^ Lewis, J., Martel, R., Trépanier, L., Ampleman, G. and Thiboutot, S., 2009. Quantifying the transport of energetic materials in unsaturated sediments from cracked unexploded ordnance. Journal of environmental quality, 38(6), pp.2229-2236. doi: 10.2134/jeq2009.0019 Free pdf download
  3. ^ Rosen, G. and Lotufo, G.R., 2010. Fate and effects of Composition B in multispecies marine exposures. Environmental toxicology and chemistry, 29(6), pp.1330-1337.Report.pdf
  4. ^ 4.0 4.1 Wang, P.F., Liao, Q., George, R. and Wild, W., 2011. Release rate and transport of munitions constituents from breached shells in marine environment. In Environmental chemistry of explosives and propellant compounds in soils and marine systems: Distributed source characterization and remedial technologies (pp. 317-340). American Chemical Society. doi: 10.1021/bk-2011-1069.ch016
  5. ^ Li, Y., Yang, C., Bao, Y., Ma, X., Lu, G. and Li, Y., 2016. Aquatic passive sampling of perfluorinated chemicals with polar organic chemical integrative sampler and environmental factors affecting sampling rate. Environmental Science and Pollution Research, 23(16), pp.16096-16103. doi: 10.1007/s11356-016-6791-1
  6. ^ 6.0 6.1 6.2 Voie, Øyvind A., and Espen Mariussen. "Risk assessment of sea dumped conventional munitions." Propellants, Explosives, Pyrotechnics 42, no. 1 (2017): 98-105. doi:10.1002/prep.20160
  7. ^ 7.0 7.1 7.2 7.3 7.4 7.5 7.6 Rosen, G., Lotufo, G.R., George, R.D., Wild, B., Rabalais, L.K., Morrison, S. and Belden, J.B., 2018. Field validation of POCIS for monitoring at underwater munitions sites. Environmental toxicology and chemistry, 37(8), pp.2257-2267. doi: 10.1002/etc.4159
  8. ^ 8.0 8.1 8.2 8.3 Beck, A.J., Gledhill, M., Schlosser, C., Stamer, B., Böttcher, C., Sternheim, J., Greinert, J. and Achterberg, E.P., 2018. Spread, behavior, and ecosystem consequences of conventional munitions compounds in coastal marine waters. Frontiers in Marine Science, 5, p.141. Report.pdf
  9. ^ 9.0 9.1 Beck, A.J., van der Lee, E.M., Eggert, A., Stamer, B., Gledhill, M., Schlosser, C. and Achterberg, E.P., 2019. In situ measurements of explosive compound dissolution fluxes from exposed munition material in the Baltic Sea. Environmental science & technology, 53(10), pp.5652-5660. doi: 10.1021/acs.est.8b06974
  10. ^ Wang, P. F., George, R. D., Wild, W. J., and Liao, Q., 2013. Defining munition constituent (MC) source terms in aquatic environments on DoD Ranges (ER-1453), Final Report. SSC Pacific Technical Report 1999. Strategic Environmental Research and Development Program (SERDP). Space and Naval Warfare Systems Center (SSC) Pacific: San Diego, CA Report.pdf
  11. ^ 11.0 11.1 11.2 11.3 11.4 Lotufo, G.R., Chappell, M.A., Price, C.L., Ballentine, M.L., Fuentes, A.A., Bridges, T.S., George, R.D., Glisch, E.J., Carton, G. 2017. Review and synthesis of evidence regarding environmental risks posed by munitions constituents (MC) in aquatic systems, Final report. SERDP Project ER-2341. ERDC/EL TR-17-17. US Army Corps of Engineers, Engineer Research and Development Center, Vicksburg, MS Report.pdf
  12. ^ 12.0 12.1 Tobias, C. 2019. Tracking the uptake, translocation, cycling, and metabolism of munitions compounds in coastal marine ecosystems using Stable Isotopic Tracer, Final Report. SERDP Project ER-2122. Report.pdf
  13. ^ Craig, H.D. and Taylor, S., 2011. Framework for evaluating the fate, transport, and risks from conventional munitions compounds in underwater environments. Marine Technology Society Journal, 45(6), pp.35-46. doi: 10.4031/MTSJ.45.6.10
  14. ^ Lotufo, G.R., Rosen, G., Wild, W. and Carton, G., 2013. Summary review of the aquatic toxicology of munitions constituents (No. ERDC/EL-TR-13-8). US Army Corps of Engineers, Engineer Research and Development Center, Vicksburg, MS Report.pdf
  15. ^ Rodacy, P.J., Reber, S.D., Walker, P.K. and Andre, J.V., 2001. Chemical sensing of explosive targets in the Bedford Basin, Halifax Nova Scotia. Sandia National Laboratories. Report.pdf
  16. ^ Porter, J.W., Barton, J.V. and Torres, C., 2011. Ecological, radiological, and toxicological effects of naval bombardment on the coral reefs of Isla de Vieques, Puerto Rico. In Warfare Ecology (pp. 65-122). Springer, Dordrecht. doi:10.1007/978-94-007-1214-0_8
  17. ^ Poulier, G., Lissalde, S., Charriau, A., Buzier, R., Cleries, K., Delmas, F., Mazzella, N. and Guibaud, G., 2015. Estimates of pesticide concentrations and fluxes in two rivers of an extensive French multi-agricultural watershed: application of the passive sampling strategy. Environmental Science and Pollution Research, 22(11), pp.8044-8057.
  18. ^ Roll, I.B. and Halden, R.U., 2016. Critical review of factors governing data quality of integrative samplers employed in environmental water monitoring. Water research, 94, pp.200-207. Open Access Manuscript
  19. ^ 19.0 19.1 19.2 19.3 19.4 19.5 19.6 19.7 Belden, J.B., Lotufo, G.R., Biedenbach, J.M., Sieve, K.K. and Rosen, G., 2015. Application of POCIS for exposure assessment of munitions constituents during constant and fluctuating exposure. Environmental toxicology and chemistry, 34(5), pp.959-967. doi: 10.1002/etc.2836
  20. ^ 20.0 20.1 Rosen, G., Wild, B., George, R.D., Belden, J.B. and Lotufo, G.R., 2016. Optimization and field demonstration of a passive sampling technology for monitoring conventional munition constituents in aquatic environments. Marine Technology Society Journal, 50(6), pp.23-32. doi: 10.4031/MTSJ.50.6.4
  21. ^ 21.0 21.1 21.2 21.3 Lotufo, G.R., George, R.D., Belden, J.B., Woodley, C.M., Smith, D.L. and Rosen, G., 2018. Investigation of polar organic chemical integrative sampler (POCIS) flow rate dependence for munition constituents in underwater environments. Environmental monitoring and assessment, 190(3), p.171. doi: 10.1007/s10661-018-6558-x
  22. ^ 22.0 22.1 22.2 Lotufo, G.R., George, R.D., Belden, J.B., Woodley, C., Smith, D.L. and Rosen, G., 2019. Release of Munitions Constituents in Aquatic Environments Under Realistic Scenarios and Validation of Polar Organic Chemical Integrative Samplers for Monitoring. Environmental toxicology and chemistry, 38(11), pp.2383-2391. doi: 10.1002/etc.4553
  23. ^ 23.0 23.1 23.2 23.3 23.4 23.5 Estoppey, N., Mathieu, J., Diez, E.G., Sapin, E., Delémont, O., Esseiva, P., de Alencastro, L.F., Coudret, S. and Folly, P., 2019. Monitoring of explosive residues in lake-bottom water using Polar Organic Chemical Integrative Sampler (POCIS) and chemcatcher: determination of transfer kinetics through Polyethersulfone (PES) membrane is crucial. Environmental pollution, 252, pp.767-776. doi: 10.1016/j.envpol.2019.04.087
  24. ^ 24.0 24.1 Alvarez, D.A., Petty, J.D., Huckins, J.N., Jones‐Lepp, T.L., Getting, D.T., Goddard, J.P. and Manahan, S.E., 2004. Development of a passive, in situ, integrative sampler for hydrophilic organic contaminants in aquatic environments. Environmental Toxicology and Chemistry: An International Journal, 23(7), pp.1640-1648. doi:10.1897/03-603
  25. ^ 25.0 25.1 Morin, N., Miège, C., Coquery, M. and Randon, J., 2012. Chemical calibration, performance, validation and applications of the polar organic chemical integrative sampler (POCIS) in aquatic environments. TrAC Trends in Analytical Chemistry, 36, pp.144-175. doi: 10.1016/j.trac.2012.01.007 Author's Manuscript.pdf
  26. ^ Seethapathy, S., Gorecki, T. and Li, X., 2008. Passive sampling in environmental analysis. Journal of Chromatography A, 1184(1-2), pp.234-253. doi: 10.1016/j.chroma.2007.07.070
  27. ^ Mazzella, N., Dubernet, J.F. and Delmas, F., 2007. Determination of kinetic and equilibrium regimes in the operation of polar organic chemical integrative samplers: Application to the passive sampling of the polar herbicides in aquatic environments. Journal of Chromatography A, 1154(1-2), pp.42-51. doi: 10.1016/j.chroma.2007.03.087
  28. ^ Arditsoglou, A. and Voutsa, D., 2008. Passive sampling of selected endocrine disrupting compounds using polar organic chemical integrative samplers. Environmental Pollution, 156(2), pp.316-324. doi: 10.1016/j.envpol.2008.02.007
  29. ^ 29.0 29.1 Harman, C., Allan, I.J. and Vermeirssen, E.L., 2012. Calibration and use of the polar organic chemical integrative sampler-a critical review. Environmental Toxicology and Chemistry, 31(12), pp.2724-2738. doi: 10.1002/etc.2011 Report.pdf
  30. ^ Godlewska, K., Stepnowski, P. and Paszkiewicz, M., 2020. Application of the Polar Organic Chemical Integrative Sampler for Isolation of Environmental Micropollutants–A Review. Critical reviews in Analytical Chemistry, 50(1), pp.1-28. doi: 10.1080/10408347.2019.1565983
  31. ^ 31.0 31.1 Li, Y., Yang, C., Zha, D., Wang, L., Lu, G., Sun, Q. and Wu, D., 2018. In situ calibration of polar organic chemical integrative samplers to monitor organophosphate flame retardants in river water using polyethersulfone membranes with performance reference compounds. Science of The Total Environment, 610, pp.1356-1363. doi: 10.1016/j.scitotenv.2017.08.234
  32. ^ Booij, K. and Smedes, F., 2010. An improved method for estimating in situ sampling rates of nonpolar passive samplers. Environmental Science & Technology, 44(17), pp.6789-6794. doi: 10.1021/es101321v
  33. ^ Harman, C., Thomas, K.V., Tollefsen, K.E., Meier, S., Bøyum, O. and Grung, M., 2009. Monitoring the freely dissolved concentrations of polycyclic aromatic hydrocarbons (PAH) and alkylphenols (AP) around a Norwegian oil platform by holistic passive sampling. Marine Pollution Bulletin, 58(11), pp.1671-1679. doi: 10.1016/j.marpolbul.2009.06.022
  34. ^ Morrison, S.A. and Belden, J.B., 2016. Calibration of nylon organic chemical integrative samplers and sentinel samplers for quantitative measurement of pulsed aquatic exposures. Journal of Chromatography A, 1449, pp.109-117. doi: 10.1016/j.chroma.2016.04.072
  35. ^ Bernard, M., Boutry, S., Tapie, N., Budzinski, H. and Mazzella, N., 2018. Lab-scale investigation of the ability of Polar Organic Chemical Integrative Sampler to catch short pesticide contamination peaks. Environmental Science and Pollution Research, pp.1-11. doi: 10.1007/s11356-018-3391-2
  36. ^ Miège, C., Mazzella, N., Allan, I., Dulio, V., Smedes, F., Tixier, C., Vermeirssen, E., Brant, J., O’Toole, S., Budzinski, H. and Ghestem, J.P., 2015. Position paper on passive sampling techniques for the monitoring of contaminants in the aquatic environment–achievements to date and perspectives. Trends in Environmental Analytical Chemistry, 8, pp.20-26. Author's Manuscript.pdf
  37. ^ Belden, J., Sims, P., Rosen, G., George, R. and Lotufo, G., 2016. Optimization of Integrative Passive Sampling Approaches for Use in the Epibenthic Environment. SERDP Project ER-2542 report.pdf
  38. ^ Lynch, J.C., Brannon, J.M. and Delfino, J.J., 2002. Effects of component interactions on the aqueous solubilities and dissolution rates of the explosive formulations octol, composition B, and LX-14. Journal of Chemical & Engineering Data, 47(3), pp.542-549. doi: 10.1021/je010294j]
  39. ^ Barton, J.V. and Porter, J.W., 2004. Radiological, chemical, and environmental health assessment of the marine resources of the Isla de Vieques Bombing Range, Bahia Salina del Sur, Puerto Rico. Underwater Ordnance Recovery, Inc.
  40. ^ Charriau, A., Lissalde, S., Poulier, G., Mazzella, N., Buzier, R. and Guibaud, G., 2016. Overview of the Chemcatcher® for the passive sampling of various pollutants in aquatic environments Part A: Principles, calibration, preparation and analysis of the sampler. Talanta, 148, pp.556-571. doi: 10.1016/j.talanta.2015.06.064
  41. ^ Warren, J.K., Vlahos, P., Smith, R. and Tobias, C., 2018. Investigation of a new passive sampler for the detection of munitions compounds in marine and freshwater systems. Environmental Toxicology and Chemistry, 37(7), pp.1990-1997. doi: 10.1002/etc.4143

See Also