HEER Office

8.4 FIELD SCREENING METHODS FOR SELECT CONTAMINANTS AND MEDIA

Information is provided below for examples of field screening methods (USEPA methods or state environmental program methods) that may be applicable for site investigations or removal/remediation work. For USEPA methods, check for the latest applicable method editions at the SW 846 methods website (USEPA, 2010). Other sources of field screening methods may be acceptable, as discussed in Subsection 8.3. Site investigation typically includes both horizontal and vertical delineation of contaminants and this should be considered when selecting applicable field sample collection and screening or analysis methods.

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8.4.1 METALS

Method 6200 (USEPA 2007g): Field Portable XRF Spectrometry for the Determination of Elemental Concentrations in Soil and Sediment

Method: XRF uses either sealed radioisotope sources or X-ray tubes (more current technology) to irradiate a soil sample. This incident radiation dislodges electrons from the innermost electron shells creating vacancies, which are filled by outer shell electrons. This rearrangement of electrons results in emission of X-rays (or X-ray fluorescence) that is characteristic of a specific atom and can be quantified. A single reading typically tests up to one-gram of sample, depending on the XRF being used. Source radiation and detector performance may vary by manufacturer and model. Field calibration standards, and calibration standards (or standard reference materials) should be employed for calibration and QA/QC measures. Those involved in sampling and testing should be trained in the use of the device and in radiation safety in accordance with manufacturer specifications and state radiation safety policy.

Detection limits vary from <10 to >200 milligrams per kilogram (mg/kg) depending on the instrument type and settings, the acquisition time used to collect a reading and the target element. The analyst should be trained in the use of the device, including XRF theory, instrument operation and calibration, detection limits, sample collection and processing, potential interferences and biases, QA/QC and data interpretation, and radiation safety (Kalnicky 2001; see also Geotek 2013,b). An overview of these issues is provided below but is not intended to serve as a replacement for formal training.

Due to advances in X-ray tube technology and difficulties in transporting radioactive materials, most field-portable XRF instruments currently use X-ray tubes. Some simple instruments have a few operating modes (i.e. alloy analysis, soil analysis, etc.) and built-in software, which provides real-time numeric concentrations for various elements. More advanced instruments allow flexibility in operational settings (tube voltage and current settings; filters for conditioning x-ray source, etc.) and collection of XRF spectra for later processing and analysis. Note that XRFs used in Hawai‘i must be registered in the State of Hawai‘i through completion of a Department of Health Radiation Facility License (https://health.hawaii.gov/irhb/radforms/). A copy of the XRFs license should be maintained by the user in the field, along with contact information for the specific entity that the XRF is registered under. Consultants who intend to bring XRF equipment in from out-of-state must ensure that the equipment is first registered and that a copy of the RFL license is included. If the specific type and model of equipment to be imported is unknown, then this can be noted on the form as “to be determined”.

XRF technology can provide comparable or higher quality data for total metal concentrations in soil in comparison to standard laboratory extraction/analysis methods, even when highly quantitative and accurate methods such as Inductively Coupled Plasma (ICP) are used by the laboratory to analyze the extract. This is primarily due to the incomplete extraction and corresponding under reporting of metals at the laboratory using common acid digestion methods (e.g., 3050B acid digest). For example, a comparison of XRF versus ICP data (Method 6010B) for soil samples collected as part of an internal HDOH project (HDOH, 2015) indicated consistently higher concentration of arsenic, copper, iron and zinc for the XRF data (average 30-60%). In some cases, however, the XRF reported a consistently lower concentration of a metal in comparison to the ICP data. In the cited example, reported concentrations of lead were similar but slightly lower (average -7%) for the XRF, possibly due to interference from moisture in the soil. The precision of laboratory data can be improved by using a more vigorous extraction method such as Method 3051A (microwave digestion). Both XRF and ICP methods have spectral overlap limitations that must be evaluated by an experienced operator of the analytical equipment.

The common laboratory USEPA 3050B acid digest method, though not as complete a digestion as stronger acid digest methods, could be considered by some to more accurately reflect “available metal” exposures for site receptors. Higher total metal analysis results for XRF and strong acid digestion methods in the laboratory can be due, in part, to metal concentrations that are bound tightly in the matrix of the soil particles and not readily bioavailable, even if the soil was ingested by a site receptor. Therefore, the choice of laboratory sample digestion methods for comparison to in situ or ex situ XRF metals data will affect the resulting correlation analysis and data interpretation, and should be considered/addressed in the site investigation DQOs and discussed with the laboratory. As in any investigation, systematic planning and clear site investigation objectives are an important part of field XRF screening investigations (refer to Sections 3 and 4 for further information). USEPA Method 6200 provides information relevant to data quality objectives specific for use of an XRF (USEPA 2007g).

Target Analytes: The number of metals that can be tested depends on the type of XRF used. Target elements of potential environmental concern at sites in Hawai‘i are typically limited to lead, arsenic and mercury (refer to Section 9). Lead is commonly found in soil impacted by lead-based paint, lead shot, and fill material that includes incinerator ash. Arsenic contamination is associated with the use of arsenic-based herbicides and can be very localized (e.g., at former pesticide mixing sites or from historic weed control around electrical substations) or widespread (e.g., due to past use for weed control in sugarcane fields). Mercury can be encountered at former sugar cane seed dipping facilities.

The need to test for and report other metals as potential contaminants of concern should be examined as part of the Systematic Planning process (TGM Section 3) and included in the site investigation work plan. Anthropogenic-related soil contamination associated with metals other than lead, arsenic, and mercury above levels of potential concern is rare in Hawai‘i. Note that naturally occurring concentrations of heavy metals in the iron-rich, volcanic soils of Hawai‘i can be significantly higher than typically found on the mainland US (e.g., cadmium, chromium, titanium, vanadium and zinc; see HDOH, 2012). These background concentrations of metals are tightly bound to soil particles (e.g., iron hydroxides) and do not pose a risk to human health and the environment (see also HDOH, 2016). Binding of arsenic residues to soil also significantly reduces the bioavailability and potential health risk posed by this contaminant (e.g., see Cutler 2011) and Cutler et al. 2013). In the case of arsenic, bioaccessibility testing data rather than total concentration data are used for human health risk and removal/remediation decision making purposes (HDOH, 2011c).

Advantages of Field-based XRF:

• In situ or ex situ analysis can be performed.
• Samples can be analyzed in minutes.
• Samples can be analyzed for multiple elements (metals) simultaneously.
• Many XRF instruments are portable and can operate in the field on battery power.
• Samples are not destroyed and can be re-analyzed or further analyzed in the lab by other methods.
• Simple sample preparation means little to no waste generation (i.e., no acids, solvents, etc.).

Limitations of Field-based XRF:

• Detection limits may vary significantly depending on the type of XRF instrument, x-ray sources, detection resolution, sample matrix, moisture content, and the metal being measured. Detection limits, depending on conditions and operating parameters can be higher than laboratory-based analytical methods, so project specific reporting limits should be evaluated to determine if XRF is appropriate, and what XRF instrumentation and operating parameters would work best.
• Physical matrix effects result from variations in particle size, uniformity and sample surface (ideally flat and smooth). If it is determined that physical matrix effects are impacting XRF measurements, these limitations can be managed by proper ex situ sample preparation including sample drying, sieving and increasing the number of points tested within a sample in order to both reduce and better represent variability within the sample.
• Moisture content can affect sample results. Field studies have indicated that the XRF fluorescence signal and calculated element concentration can be reduced by as much as 1 percent for every 1 percent increase in soil moisture (Cutler 2009). This limitation can be initially evaluated by pre-testing soil samples from the site under both field-moist and dried conditions. Potential interference from moisture can also be managed by uniformly drying (ex situ) samples before analysis (air or oven drying at <40°C preferred). Alternatively, moisture content can be determined in samples after field XRF analysis in field-moist condition, and results corrected for moisture effect (analogous to a laboratory reporting concentration in dry weight basis after applying a moisture correction). To perform such moisture correction, a calibration curve between XRF response and moisture content for each element of interest is required.
• Different metals can produce XRF spectral responses that interfere with one other because of peak overlap or absorption/enhancement phenomena. Most of these interferences are corrected automatically by modern XRF instrument software or post-acquisition software; however, they are best handled by calibration using site-specific calibration standards (SSCS), as described below. Hawaiian soils derived from volcanic materials contain high concentrations of iron (up to 20% by weight), titanium (up to 5%) and other heavy metals. The presence of these metals can greatly reduce fluorescence intensity of other elements (e.g., refer to Geotek 2013). For example, high iron can interfere with the accurate analysis of cobalt. Reported chromium concentrations can be falsely elevated in the presence of iron. High titanium can interfere with analysis for barium. Obtaining accurate element concentrations in high-iron soils (or sediments) requires use of calibration standards with similar atomic density, or better yet the use of SSCSs.
• Quantification of arsenic with elevated lead can be problematic due to fluorescence peak interference (USEPA 2007), as the dominant lead peak (L-alpha) emits at the same energy as the dominant arsenic peak (K-alpha). Lead concentrations can be readily determined from an alternate (secondary) peak; however, the arsenic secondary peak, depending on the instrument, might be too weak for quantification at concentrations of interest (e.g., below the Hawai‘i background concentration of 24 mg/kg). Newer XRF instruments and their robust built-in analysis software do an excellent job of quantifying lead and arsenic based on analysis of multiple fluorescence peaks. If analyzing samples for arsenic in the presence of lead, a subset of samples should be analyzed by laboratory methods to confirm XRF accuracy.
• A specific license, including a radiation safety course, is required to operate some XRF instruments that have radioactive source materials (hence most portable units now utilize x-ray tubes). Follow instrument-specific instructions to ensure proper operation of equipment. Persons using the instrument, or working in the vicinity of the instrument, should be trained on x-ray safety as per instrument guidance.

HEER Office recommendations (see also Geotek 2013b):

Calibration Standards

• Calibration standards (standard reference materials [SRMs]) are materials with similar chemical and physical properties as site samples, but with known concentrations of the elements of interest, analyzed in conjunction with site samples (unknowns) to allow calculation of element concentrations in unknowns. SRMs are often provided with rental XRF instruments, or can be obtained through entities such as National Institute of Standards and Technology (NIST).
• Some XRF instruments have pre-defined calibrations for “typical” soil materials built into “canned” instrument software (“fundamental” calibration). Results using these calibrations should be verified with laboratory testing of the same sample, taking into account potential laboratory processing/extraction error.
• Site-specific calibration standards (SSCSs) are also recommended in order to address differences in commercial SRMs (Standard Reference Materials) and local soils. Samples of soils from the study site (or a site with similar soil type) are collected prior to field work. Elements of interest are determined by laboratory analysis using EPA analytical methods (e.g., for most metals, acid digestion by 3050B [often incomplete digestion] or 3051 [more complete digestion since it employs microwave heating] and ICP analysis of digest by 6010 [ICPES] or 6020 [ICPMS]). Either contaminated site samples (unspiked) or spiked (element of interest added at known concentration) samples can be used as SSCSs. Spikes can be prepared, for example, by drying and sieving a sample (typically a site sample screened by XRF to have low concentrations of the element of interest) to an appropriate grain size (<2mm for most site assessments), spiking the sample with the element(s) of interest to generate a desired screening concentration, and then analyzing the sample by laboratory methods for verification of the spiked concentration. High-quality SSCSs can be prepared at the laboratory and analyzed using a nearly complete acid extraction (e.g., USEPA Method 3051) and Inductively Coupled Plasma Mass Spectrometry analysis (ICP-MS). Two or more spiked samples that cover the potential range of contamination anticipated are typically prepared for use as SSCSs in the field (e.g., 50 mg/kg, 200 mg/kg and 1000 mg/kg for arsenic). These SSCSs can subsequently be used throughout a study to either: 1) confirm instrument performance in the field or 2) create a calibration curve to correct instrument readings to final reported concentrations.
• The XRF should be calibrated daily during field work per manufacturer specifications using commercially available Standard Reference Materials (SRMs) such as those supplied by National Institute of Standards and Testing (NIST) or SSCSs. This typically includes soil standards with known metal concentrations (e.g., NIST 2010) but can also include manufacturer-provided stainless steel coins and other materials. Include a known, low-concentration sample to check the instrument reporting level for targeted metals (e.g., a lab-supplied sample or preferably a SSCS). Following the calibration, a blank should be analyzed to confirm negative control (e.g., NIST silicon blank). These materials are typically provided along with an XRF instrument if rented from a commercial vendor. The NIST metal standard or preferably a SSCS should then be used to confirm positive control.
• More detailed, calibration curves to improve the accuracy of field data can be developed by comparison of XRF and laboratory analysis data for splits of multiple samples across a range of metal concentrations (e.g., see Cutler 2009). The resulting data can be used to develop algorithms for adjustment of XRF-generated concentrations to equivalent laboratory method concentrations. A minimum of 3-4 SSCSs are recommended for initial development of a calibration curve (more if a good linear calibration curve is not achieved over the measurement range of interest).
• Caution is advised for comparison of field XRF data against laboratory data. Sample preparation (e.g., drying, sieving and subsampling), sample heterogeneity (e.g., inadequate number of sample points analyzed in field), and laboratory acid digestion methodology (e.g., Method 3050B versus 3051A) are far more likely to be the cause of conflicting results than the analytical method used to test the sample (XRF versus ICP).
• Samples from the site (or a site with similar soil type and climate setting) should also be collected (prior to the primary investigation) to test for matrix suitability and potential interferences. For example, soil moisture is known to interfere with XRF readings. Prior to the investigation, samples can be collected during rainfall conditions similar to anticipated conditions during the actual investigation. Tests made on both moist and dried samples can provide information on potential moisture interferences in the field. This can be used to calibrate the XRF prior to field screening to account for moisture interference.

Ex situ XRF Screening

• Ex situ screening of soil is likely to provide more representative and useful data than in situ analysis. In situ testing is prone to error due to small-scale random, small-scale variability of metal concentrations in soil as well as matrix interferences (refer to Subsection 4.1.2).
• A Decision Unit (DU) should be designated for a specific area of interest (e.g., suspect Spill Area DU or targeted Exposure Area DU; refer to Subsection 3.4). A Multi Increment sample consisting of 30-75+ increments should then be collected from the targeted DU and tested in the field using a portable XRF (see Subsection 4.2 and Section 5).
• Alternatively, a grid of “discrete” sample points can be used to help identify large-scale patterns of contamination and designate DUs for more detailed characterization (refer to Subsection 4.3). The collection of traditional 100-200g discrete soil samples from a single location is not recommended due to the uncertainty imposed by potential random, small-scale variability of contaminant concentration around individual grid points (see Subsection 4.1.2). As an alternative, large-mass discrete samples can be prepared by the collection of a minimum of 300g of soil from multiple points (e.g., 5-10+) within a short distance (e.g., one meter) of a grid point (see Subsection 4.3). This will improve the representativeness of the sample data for the subject grid point.
• Samples should be manually mixed to reduce variability prior to XRF testing, but be aware of separation of fines from coarser material. Coarse material should be removed prior to testing (e.g., >2 mm; plant roots, stones, etc.). If samples are dry enough, field sieving to the <2 mm size fraction and mixing can reduce small-scale variability and improve measurement accuracy. Potential interference from moisture can be addressed by drying samples before analysis (air or oven drying at ≤40°C preferred). Alternatively, the moisture content of field samples can be determined after analysis and results corrected, if a calibration curve between XRF response and moisture content for each element of interest has been determined.
• Spread the sample (typically in a plastic bag) to a thickness of 1 to 2 centimeters in order to allow equal access to all portions of the soil sample for X-ray analyses. A minimum of 10 to 20 random locations within the sample (representing a total of at least 10 grams of soil, assuming 0.5 to 1.0 grams tested per reading) should be tested until a reasonably consistent mean can be established that is unlikely to significantly change with additional testing (target a relative standard deviation of ≤20% to determine adequate number of readings). Test locations on both sides of the bagged, spread-out sample.
• Compare the average of the readings for a sample to action levels for decision making (refer to Subsection 3.2.1 and Subsection 3.4). Note that small-scale variability within an MI sample (or between discrete samples) is not important in terms of risk. HDOH EALs are likewise not intended for comparison to individual, discrete sample data for more than qualitative, screening level purposes (refer to Subsection 4.3).
• The following additional preparation and analysis procedures can be used to improve the quality and reliability of ex situ XRF data: 1) Prepare SSCSs to improve XRF measurement accuracy, 2) Inspect raw XRF spectra to ensure data acquisition is executed properly and assess potential interference from overlapping peaks (e.g., arsenic and lead), and 3) Grind (mill) samples to reduce variability if needed and practical for field screening (e.g., check variance of multiple analyses on subsamples of a larger sample to determine whether grinding may be necessary to reduce variability).

In situ XRF Screening

• In situ XRF measurements can be used for collection of semi-quantitative data to: 1) Identify potential metals of concern in soils or sediments, 2) Approximate extent of contamination on the project site and aid in the designation of DUs, and/or 3) Aid in determining locations for collection of MI samples for ex situ measurements.
• In situ samples generally consist of exposed surface or subsurface soils (i.e. excavation sidewalls) and are analyzed by XRF in place. User’s should be aware that single, in situ tests are highly prone to error associated with random, small-scale heterogeneity (i.e., variability over a few inches; refer to Subsection 4.1). Soil contaminant concentrations at the scale of an individual XRF reading can vary dramatically over short distances. Slightly offset, replicate measurements should be taken at each location to improve accuracy for the targeted sample location. Be aware that concentrations can also vary significantly and randomly over distances of a few feet, and patterns suggested by individual test points are also prone to error.
• Readings should be biased to areas of finer-grained soil (i.e., <2 mm particle size), and avoid taking readings on rocks or other large debris. Use a trowel or similar device to lift grass and organic material away from the targeted soil. A small piece of polyethylene film or similar material should be placed against the soil in order to protect the XRF detector. Detector window films (typically mylar) can easily rupture. The detector should not be used in any capacity with a ruptured window film. Care should be taken when replacing a window film to not allow soil or dust to enter the instrument.
• Ensure the XRF instrument can tolerate rain conditions, if encountered. Use a plastic bag or other rain protection for the instrument when needed in the field, or consider collecting ex situ samples and testing them at a fixed and protected location on- or off-site.
• Follow manufacturer specifications regarding acquisition time for the sample analysis (e.g., 30 second measurement typically recommended). Longer acquisition times can improve reporting levels, and may be desirable in certain situations.
• SSCSs are recommended if improved measurement accuracy is needed. If only relative element concentrations are required, default instrument calibrations or commercial standard reference materials (SRMs) can be used for calibration.

Additional Information:

• Printout of raw, XRF data for the project that includes calibration data and corresponding sample ID numbers (include as an appendix);
• Summary of ex situ sample collection methods including DU designation, number of increments collected, tools used, sample container, approximate sample mass, etc., and/or summary of in situ testing method used;
• Summary of field processing, including removal of large material, moisture testing, drying and subsampling, as applicable;
• Preparation of site-specific calibration standards, if used;
• Summary of XRF instrument utilized, including maker, beam strength used, calibration method, and other pertinent information;
• Summary of XRF testing method, including targeted metals, XRF read time, number of points tested, problems encountered in the field, etc.,
• Summary of XRF data and laboratory data comparison and, if prepared, calibration curves based on site-specific samples;
• Discuss how the XRF data were used for decision making in the field and will be used for any subsequent investigation work, and other information pertinent to the project.

Case Study – Arsenic at a Pesticide Mixing Site (see also Cutler 2009):

Elevated arsenic was identified in MI samples collected from a nine-acre, former pesticide mixing area. The past history of the site suggested that contamination was likely to be localized in the northwestern area of the property. In order to confirm and expedite identification of this area, ninety discrete soil samples with a mass of a few hundred grams each were collected in a grid pattern across the property and analyzed for total arsenic with a field-portable XRF. A subset of these samples was analyzed offsite for both total arsenic (USEPA Methods 3050B/6020) and bioaccessible arsenic (environmental hazards from direct contact to arsenic-contaminated soil are managed in the State of Hawai‘i by evaluating bioaccessible arsenic). From this data a correlation was developed between the total arsenic (measured by XRF) and bioaccessible arsenic. This allowed initial estimate of the area and volume of contaminated soil above bioaccessible arsenic thresholds, and better cost estimates for evaluation of remedial alternatives. Confirmation sampling using the DU/MIS process will be guided by the discrete sampling and field XRF analysis results.

The XRF data indicate a core area of arsenic contamination in the location of a known, former pesticide mixing area on the property. The model-generated sharpness of boundaries between “clean soil” and “contaminated” soil is misleading, however, and gives a false sense of resolution (see Section 4). As the mean concentration of arsenic in the soil situated between the heavily contaminated area and the apparently clean area begins to approach the target action level, smaller-scale variability in concentrations within the soil will begin to be exhibited in the form of seemingly isolated “hot spots” and “cold spots” above and below the target action level. These spots are “real” in terms of the soil samples tested, but cannot be accurately extrapolated beyond the mass of the soil tested with any degree of certainty, based on the discrete sample data alone. The identification of a hot spot or cold spot at any given location within this transition zone could instead be purely random in nature. If additional samples were collected a short distance away, then concentrations could be reversed, with “hot spot” areas turning “cold” and vice versa. Removal of isolated, sample-size hot spots is unlikely to reduce the overall, mean concentration of arsenic within this zone. Perimeter DUs should instead be designated for these areas and MI samples used to estimate mean contaminant concentrations for comparison to action levels (refer to Section 3).

This type of heterogeneity-derived variability is commonplace in attempts to generate isoconcentration maps from large amounts of discrete data. Such patterns are readily apparent in maps of background metals in soil published by the US Geological Survey (USGS 2014). As stated in that document:

“Soil geochemistry can vary considerably over (the distance between sample points), and this variation will not be accurately portrayed by the (isoconcentration) interpolation procedure. This study… (was) designed to reveal regional-, national-, and continental-scale geochemical and mineralogical patterns extending over thousands or hundreds of thousands of square kilometers. The resulting data sets are not appropriate for the accurate estimation of the concentration of a given element or mineral at a site (location) where a sample was not collected.”

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8.4.2 PETROLEUM

Current field screening methods are not capable of separately reporting TPH aromatic and aliphatic fractions. If needed, contact the laboratory for more detailed information on these types of analyses.

USEPA 4030 (USEPA, 1996l): Soil Screening for Petroleum Hydrocarbons by Immunoassay

Method: Test kits are commercially available for this method and the manufacturer’s directions should be followed. The soil sample is extracted, filtered, and the sample extract and an enzyme conjugate reagent are added to immobilized antibody. The enzyme conjugate competes with the TPH present in the sample for binding to the immobilized anti-TPH antibody. The test is interpreted by comparing the sample response to a reference response.

Target Analytes: Depending on the testing product selected, results can be used to determine relative levels of TPH (low, medium, high) or whether the sample exceeds a threshold concentration (5, 25, 100, or 500 mg/kg).

Advantages:

• Samples can be analyzed quickly and on-site.
• Method is not affected significantly by moisture content or pH.

Limitations:

• Small mass of soil tested;
• The sensitivity of any immunoassay kit depends on the binding of the target analyte to the antibodies used in the kit. These kits are most sensitive to small aromatic compounds (ethylbenzene, xylenes, and naphthalene), while petroleum fuels tend to be dominated by aliphatic compounds.
• Non-TPH compounds such as chlordane and toxaphene show cross reactivity and can cause false positives.
• The sensitivity of the test is influenced by the nature of the hydrocarbon contamination and any degradation processes at the site. Although the response of the test to different sites will vary, the results within a site should be consistent and could be interpreted with comparison to laboratory TPH data.
• Organic and clay-rich soils may limit the effectiveness of soil extraction and may require longer extraction times than other soil types.

HEER Office recommendations: The HEER Office recommends an initial site-specific evaluation of this method. Laboratory confirmation data required for final decision making.

Method: A sample of soil is extracted with a solvent mixture (primarily methanol), filtered, and added to an aqueous emulsifier development solution. As a result the hydrocarbons precipitate out and become suspended in solution. The sample is measured in a turbidimeter using a beam of yellow light at 585 nanometers (nm). Commercially available turbidimetric kits include the PetroFLAG™ system (see also USEPA 2001f).

Target Analytes: Broad spectrum of petroleum hydrocarbons in the range of 10 to 2000 parts per million (ppm).

Advantages: Samples can be analyzed quickly on-site, and at low cost. Most test kits do not require power or use battery-operated components.

Limitations:

• Small mass of soil tested;
• Potential under reporting of TPH concentration due to evaporation of volatile petroleum hydrocarbon mixtures such as gasoline during test procedure.
• Organic-rich soils can cause a positive interference as naturally occurring compounds become suspended in solution and/or cause a negative interference due to a reduced effectiveness of the extraction.
• Extraction may be difficult with clayey soils.
• Higher moisture content will bias sample results lower because there is a resultant dilution of the extraction solvent.
• The response of individual PAHs varied greatly from compound to compound and therefore use of this method to quantify individual PAHs is not recommended although quantification of PAHs as part of a larger hydrocarbon fraction, such as diesel fuel is recommended.
• Temperature has an effect on the suspension and it is important to recalibrate if temperatures change more than 10 degrees.

HEER Office recommendations: The HEER Office recommends an initial site-specific evaluation of this method. Laboratory confirmation data required for final decision making purposes.

Method: This hand-held instrument uses diffuse reflectance infrared spectrophotometry to measure non-volatile TPH compounds (C10 to C36) in soils (see Figure 8-4). It was developed in collaboration with the (Australian) Commonwealth Scientific Industrial Research Organization (Forrester et al., 2012)). It is portable, hand-held, designed for regular field use, and makes direct surface soil measurements (either surface soil or along the surface of soil cores). This device is especially useful to screen for middle distillate fuels (e.g., diesel, kerosene, etc.) and heavier hydrocarbons in soil. Carbonates and natural organic matter can interfere with the infrared signature but this can be accounted for with site-specific calibrations. Moisture contents greater than 5% can also interfere with readings. Air-drying of samples is recommended for best accuracy.

Data Use: Screening.

Target Analytes: Total petroleum hydrocarbons, (C10 to C36) in soils.

Advantages:

• Portable, samples can be analyzed quickly on-site.
• Easy to calibrate in the field
• Minimal sample preparation (primarily just air-drying the surface of the soil, if >5% moisture content.

Limitations:

• Small mass of soil tested. Affected by soil moisture content – air drying before measurement is recommended.
• High cost for purchase (rental may be a more affordable option for limited use)

HEER Office recommendations: The HEER Office recommends an initial site-specific evaluation of this method. Laboratory confirmation data required for final decision making.

USEPA Innovative Technology Verification Reports (USEPA, 2008): Note: Various field testing methodologies are evaluated and detailed in “Verification Reports”. For example, two field measurement technologies evaluated and judged reliable for TPH in soil include: 1) the Remediaid TPH Starter Kit (USEPA, 2001g) and 2) the UVF 3100 TPH Analytical Test Kit (USEPA, 2001g).

Remediaid TPH Starter Kit (USEPA, 2001g):

Method: Measurement based on a combination of the modified Friedel-Crafts alkylation reaction and colorimetry. Dichloromethane is used as a reactant and the solvent to extract petroleum hydrocarbons. Anhydrous aluminum chloride is used as another reactant. At least five grams of soil can be utilized per analysis.

Data Use: Screening.

Target Analytes: Aromatic petroleum hydrocarbons in soil. Includes analysis for a number of petroleum products/fractions, including gasoline, diesel, crude, lube oil, BTEX, and PAHs.

Advantages:

• Can measure a wide range of petroleum products
• Is not sensitive to common chlorinated solvents
• Portable and battery powered colorimeter
• Can be operated by one person with basic wet chemistry skills

Limitations:

• Provides little response for MTBE or Stoddard solvent
• Minor sensitivity to soil moisture

HEER Office recommendations: The HEER Office recommends an initial site-specific evaluation of this method. Laboratory confirmation data required for final decision making.

Method: Soil measurement utilizes an ultraviolet fluorescence spectrophotometer. The fluorometer uses a mercury vapor lamp as its light source. Petroleum compounds in soil sample are mixed and extracted with methanol, and the extract is transferred to a quartz cuvette that is placed in the fluorometer. 10 gram soil samples can be analyzed.

Data Use: Screening.

Target Analytes: The test kit can measure gasoline range organics (GRO) and extended diesel range organics (EDRO) separately, by selecting the appropriate emission filter that corresponds to the wavelength those fractions will fluoresce.

Advantages:

• Method detection limits below 10 mg/kg.
• Can be operated by one person with basic wet chemistry skills
• Non-petroleum compounds (e.g. chlorinated solvents, humic acid) do not interfere

Limitations:

• Portable, but needs power source (can use 110-volt or 12-volt outlet from automobile)
• Provides little response for MTBE or Stoddard solvent
• Minor sensitivity to soil moisture

HEER Office recommendations: The HEER Office recommends an initial site-specific evaluation of this method. Laboratory confirmation data required for final decision making.

Method: A sample of soil is extracted and filtered using a commercially available test kit. The sample extract and an enzyme conjugate reagent are added to immobilized antibody. The enzyme conjugate competes with the PAHs present in the sample for binding to the immobilized anti-PAH antibody. The test is interpreted by comparing the sample response to a reference response.

Data Use: Screening.

Target Analytes: The test is most sensitive to three (phenanthrene, anthracene, fluorene) and four (benzo[a]anthracene, chrysene, fluoranthene, pyrene) ring PAH compounds and also recognizes most of the five and six ring PAHs listed in USEPA Method 8310. This test detects PAHs present at concentrations above 1 mg/kg.

Advantages: Samples can be analyzed quickly, on-site, and at relatively low cost.

Limitations:

• Small mass of soil tested;
• The sensitivity of the test is influenced by the nature of the hydrocarbon contamination and any degradation processes at the site. Although the response of the test to different sites will vary, the results within a site should be consistent and could be interpreted with comparison to laboratory PAH data.
• Field extraction of PAHs may be less effective than the extraction methods used in a laboratory and excessive amounts of oil in soil samples will interfere with the analysis of PAHs.
• Alkyl-substituted PAHs, chlorinated aromatic hydrocarbons, and other aromatic hydrocarbons (dibenzofuran) have been demonstrated to be cross-reactive with the immobilized anti-PAH antibody. The presence of these compounds may contribute to false positives.
• Kits may be damaged if frozen or if exposed to prolonged heat.

HEER Office recommendations: The HEER Office recommends an initial site-specific evaluation of this screening method for each project. Given the uncertainties with the PAH analyses, laboratory confirmation is recommended.

Method: A photoionization detector (PID) uses an ultraviolet (UV) light source to break down chemicals into positive and negative ions that can then be measure with a detector (see USEPA Field Analytic Technologies link in Table 8-2; refer also to RAE Systems 2010). A soil sample is placed in an approved container and the volatile constituents are allowed to come to equilibrium. A minimum 200 gram sample is recommended. The headspace is measured with an isobutylene calibrated PID, and a result expressed in parts per million by volume (also see Subsection 8.6.4). Double layer, metalized polyester/low-density polyethylene bags are recommended as sample containers (e.g., Associated Bag Company Item #183-52) in order to minimize vapor loss during the recommended fifteen- minute equilibration period.

The Maine guidance recommends the following approach:

• Label and open the bags;
• Unfold the bottom gusset to facilitate a uniform headspace volume;
• Place appropriate mass of soil in metalized bag (recommended minimum 200 g);
• Close bag leaving uniform headspace.
• Knead samples (in closed bag) if needed to break up clumps;
• Shake bags for 30 seconds;
• Let stand for 10 minutes (out of direct sunlight) in order for the headspace to equilibrate with the soil;
• Knead/shake bags for additional 30 seconds;
• Let stand for 2 minutes
• Note: the PID reading must be made within 30 minutes of sampling to minimize loss;
• Open bag carefully and insert probe of calibrated PID one third to half way into bag (approximately 4 inches);
• Seal bag as much as possible around probe;
• Allow instrument to read until concentrations start to fall;
• Record highest sustained reading.

Headspace concentration readings must be kept within the PIDs linear range or use the data as minimum concentrations if over the linear range. Concentrations over the linear calibration range could saturate the detector and the instrument may not be able to distinguish between higher levels of volatile compounds. Readings above the linear calibration response range used for the particular PID should be estimated as above the upper calibration concentration utilized (different brands of PIDs could have different linear response ranges, or the documented linear response range could be limited by the calibration standards available).

Either MI or samples collected from individual points can be screened. The HEER office recommends that MI samples be screened when feasible, in order to ensure adequate coverage of the targeted DU area and better represent the results of final confirmation soil samples. If samples from single points are used, then soil should be collected and combined from multiple locations within the immediate vicinity of the sample point in order to reduce the effects of random, small-scale heterogeneity. An adequate number of samples to cover the targeted area should be screened based on professional judgment in the field.

The Maine guidance provides specific PID screening levels than can be used for final, site closure decisions. For example, based on studies conducted by that agency, 200 grams of soil with 25 mg/kg TPHg placed in a 2.5 liter bag should generate a headspace reading of approximately 40 ppmv (based on MiniRAE PID readings, other PIDs may differ). This may prove useful for general screening purposes in the field. Assuming a near linear correlation at low TPHg concentrations in soil, a PID reading of 160 mg/kg would presumably reflect the HEER office Tier 1 EAL of 100 mg/kg for TPHg. A lower PID screening level of 100 ppmv is recommended due to Hawaii’s warmer climate (Maine study carried out under controlled temperatures of approximately 70ºF). A PID screening level of 10 ppmv is recommended for soils impacted with middle distillate fuels (e.g., diesel and JP-8) or when the fuel type is unknown. This corresponds to anticipated lower vapor emissions from soils containing 100 mg/kg TPHd in comparison to gasoline-contaminated soils, due to a lower proportion of light-end aromatics and aliphatic compounds in these fuels (assumed 10% of gasoline vapor emissions; see also HDOH, 2012). Consultants report that PID readings below 10ppmv are unreliable for screening purposes and can in particular be biased high due to moisture.

The Maine guidance recommends testing of very small discrete samples under some closure scenarios in order to obtain accurate readings for high PID readings. For example, the guidance recommends the use of a five-gram sample (approximately one teaspoon) and PID reading of 1,500 ppmv (using a MiniRAE PID) in order to assess potential direct-exposure risk to workers with respect to a target soil screening level of 5,000 mg/kg TPHg (the correlation of PID readings and soil concentrations are not strictly linear between low and high TPH concentrations in the Maine study.) Use of a small mass of soil in the 2.5L headspace bag is intended to ensure that the PID detector does not become saturated. At this time, the HEER office has not adopted PID screening levels for final decision making purposes, so concerns of PID saturation and the use of a small sample mass are not applicable and screening of larger and more representative samples continues to be preferred (e.g., MI sample collected from excavation floor or targeted core interval).

Data Use: Screening.

Target Analytes: Gasoline-related volatile aromatic compounds. PIDs are not good indicators of total TPH levels in soil vapors because they do not respond well to aliphatic volatile compounds, which dominate vapors from petroleum fuels (refer to Section 7 and Section 9).

Advantages:

• Samples can be analyzed quickly, on-site, and at low cost.
• Amenable to testing of large samples, including MI samples.
• PID reading cleanup levels presented in Maine DEP guidance can be used for general guidance but collection of soil confirmation samples and comparison to HDOH EALs is currently required for regulatory concurrence.

Limitations:

• Applicable only for soils contaminated with gasoline. Can also be used to screen for diesel, kerosene, JP-8 or other middle distillate fuels in soil but PID response is significantly lower than for an equivalent concentration of gasoline due to low, aromatic content of vapors.
• Requires use of a container that minimizes loss of volatile chemicals during the equilibration period.
• PID requires periodic calibration in field.

HEER Office recommendations: The HEER Office recommends an initial site-specific evaluation of this method. Laboratory confirmation data required for final decision making.

Method: Soil is added to a sample bottle with water and a rapidly dissolving red or blue oleophilic dye. Contents are shaken vigorously. Released petroleum attaches to a polystyrene bead or to the walls of the container. Bead will turn pink or blue, depending on the dye use, if the concentration of petroleum in the soil exceeds the method detection limit (e.g. 500 ppm). Kits tested by Maine DEP include Oil-In-Soil and Oil-Screen-Soil but similar kits may be available from other venders. Red dyes typically most visible. Indigo blue kits available if soil color interferes with interpretation of red dye test kits. Recommended for testing of diesel, kerosene, JP-8 or other middle distillate fuels in soil.

Data Use: Screening.

Target Analytes: Oleophilic, petroleum hydrocarbon compounds (see also petroleum discussion in Section 9).

Advantages:

• Samples can be analyzed quickly, on-site, and at low cost.
• Results can be assessed in terms of “saturated,” “positive,” “slightly positive” and “undetected.”

Limitations:

• Marketed kits only allow testing of small masses of soil (e.g., ten grams of soil placed in 50 ml bottle); may not be practical for screening of MI samples (30 g mass typically tested by laboratory).
• Not applicable for gasoline (only) contaminated sites, heavy crude oils (Bunker C), or bituminous materials like asphalt or waxes.
• Mineral oil and motor oils may be detectable, but detergents in some synthetic oils can interfere with color development in the kits (i.e., potential for false negatives).

HEER Office recommendations: The HEER Office recommends an initial site-specific evaluation of this method.

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8.4.3 PCBS

Method: Test kits are commercially available for this method. A sample of soil and an enzyme conjugate reagent are added to immobilized antibody. The enzyme conjugate “competes” with PCB present in the sample for binding to immobilized anti-PCB antibody. The test is interpreted by comparing the response produced by testing a sample to the response produced by testing a standard(s) simultaneously.

Data Use: Screening.

Target Analytes: PCBs in soils and non-aqueous waste liquids present at concentrations above 5, 10, or 50 mg/kg.

Advantages: Samples can be analyzed quickly and on-site at a lower cost than typically charged by fixed laboratories.

Limitations:

• Small mass of soil tested (typically 5-10g);
• Detection limits for PCBs may not be adequate in either of the field screening methods to meet HDOH action levels. While useful in identifying areas of high concentration, areas with low-level concentrations may be overlooked.
• Poor extraction and correlation to laboratory sample data noted by some consultants for soils with a high clay or organic carbon content;
• Depending on the test kit used, chemically similar compounds (e.g., petroleum hydrocarbons) may exhibit cross-reactivity and produce a false positive test result.

This test method cannot differentiate between different Aroclor mixtures or individual congeners.

HEER Office recommendations: The HEER Office recommends an initial site-specific evaluation of this method. Laboratory comparison data required for final decision making purposes.

Method: This electrochemical method can be used to determine the amount of polychlorinated biphenyls (PCBs) contamination in soils if PCBs are known to be the sole organic halogens at the site. Chlorine is removed from the PCB molecule using an organo-sodium reagent. The method is designed to provide quantitative field results over a range of 2 to 2,000 microgram per gram (μg/g, equivalent to mg/kg) PCBs. The test can be useful when screening soil for disposal based on the TSCA-based limit of 50 mg/kg PCBs for municipal landfills. Caution should be used, however, when using results for decision making purposes on discrete samples rather than MI samples.

Data Use: Screening.

Target Analytes: PCBs in soils and non-aqueous waste liquids present at concentrations above 5, 10 or 50 mg/kg.

Advantages: Samples can be analyzed quickly and on-site. Most test kits do not require power or use battery-operated components.

Limitations:

• Small mass of soil tested (typically 5-10g);
• Reacts to all sources of organic chlorine and the presence of chlorine-containing compounds other than PCBs will cause the analyzer to produce false positive results (e.g., organochlorine pesticides such as Technical Chlordane).
• Iodine and bromine containing compounds will also affect results if present in significant quantities.

HEER Office recommendations: The HEER Office recommends an initial site-specific evaluation of this method. Laboratory comparison data required for final decision making purposes.

Method: Method 9079 uses a colorimetric test kit to screen for PCBs in transformer oil at preset levels of 20, 50, or 500 mg/kg based on total organic chlorine detection. Samples are extracted in the field using an organo-sodium reagent. The resulting chloride ions in the sample are measured using a colometric indicator. Test readings typically calibrated to Arochlor 1242 (a lower chlorine content Arochlor) to provide conservative results. The test can be useful when screening transformer oil for TSCA-based limits for disposal options.

Data Use: Screening.

Target Analytes: PCBs in transformer oil present at concentrations above 20 mg/kg.

Advantages:

• Samples can be analyzed quickly and on-site. Most test kits do not require power or use battery-operated components.
• Results considered conservative, so concentrations near (but under) the set points typically provide a positive result, and limit false negative results.

Limitations:

• Water in the sample above 2% will cause low readings and cause a noticeable reaction with the sodium reagent.
• Can only be used for transformer oil, not for PCB contamination in other types of oils.
• Reacts to all sources of organic chlorine and the presence of chlorine-containing compounds other than PCBs will cause the analyzer to produce false positive results (e.g., organochlorine pesticides such as Technical Chlordane).

HEER Office recommendations: The HEER Office recommends an initial site-specific evaluation of this method. Laboratory comparison data required for final decision making purposes.

Method: This method uses a commercially available enzyme immunoassay (EIA) kit based on a polyclonal antibody specific for PCDD/PCDFs. The kit response correlates with total sample TEQ because the antibody responds to the 17 targeted PCDD/F congeners in approximate correlation with their toxic equivalency factors (TEFs). The kit response to a sample is a single result representing the aggregate of the individual congener responses. Congener separation is not required to use this kit, nor is it possible to generate any congener specific data with the kit.

The sample extraction and one step cleanup specified in the original Method 4025 allowed for only semi-quantitative screening at roughly 500 pg/g. That method remains viable, but the performance of the immunoassay has been improved by substituting a more conventional extraction and a simple and rapid coupled column cleanup. Quantitative analysis is possible to low pg/g levels in soils using the modified method. Detailed information is available from the immunoassay kit manufacturer, which also makes the sample preparation columns. The quantitative performance of this method has been validated by the SITE Program in two separate phases (USEPA 2008f). The effectiveness of the rapid sample preparation (separate from the immunoassay) is indicated by the fact that it is used by numerous labs for cleanup of sample extracts prior to analysis by Method 8290/1613B. Because of these improvements the immunoassay method using the coupled column cleanup is referred to as Method 4025m by the kit manufacturer and most users, to distinguish it from the original Method 4025 (Cape Technologies 2009).

Although an extremely useful screening method, EPA 4025 or its modified version (and other dioxin methods) should not be mistaken for a readily used field method. Mobilization into the field would likely require infrastructure comparable to mobilizing for the field execution of laboratory methods such as 8260, 8015, 8270 etc. (excluding expensive analytical instrumentation).

Data Use: Quantitative data at preselected decision levels (requires comparability analysis with GC/MS data; see Subsection 8.2)

Target Analytes: PCDD/PCDFs in soil to 5pg/g (ppt)(pg/g; equivalent to ng/kg or parts per trillion).

Limitations:

• Common organic solvents such as hexane, acetone, and toluene are required for sample preparation;
• Method requires fume hood but can be done in small field lab (note that no liquid acids such as fuming sulfuric are used in 4025m);
• Sample processing and cleanup procedures may limit field use of the kits, although use in a laboratory setting can reduce costs in comparison to GC/MS methods.

HEER Office recommendations: The HEER Office recommends that dioxin levels be confirmed on 10% of the samples using laboratory GC/MS analyses (but at least 3 samples, whichever is greater). The GC/MS analyses should be conducted on samples with the highest-reported, bioassay TEQ dioxins results.

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Figure 8-7.Schematic of sample processing steps for use of CALUX bioassay kit for Dioxins and PCBs (Xenobiotic Detection Systems, USEPA Method 4435).

In order to evaluate the accuracy and precision of this dioxin bioassay kit for soils in Hawai‘i, the HEER Office collected 25 multi-increment soil samples from a former sugar cane field in west O‘ahu and tested the samples for toxic equivalent (TEQ) dioxins using both High Resolution GC/MS and CALUX, USEPA Field Screening Method 4435 (HDOH, 2007e). The study showed that CALUX consistently over predicted TEQ dioxin concentrations in the soil in comparison to the GC/MS analysis. Dioxin TEQ concentrations estimated by CALUX ranged from 96% to 631% higher (average 297%) than Method 8290 data for splits of the MI samples. The difference was significantly higher for samples collected from an adjacent field, with CALUX data ranging from 416% to 1,346% higher (average 905%) than Method 8290 data for splits of the same samples (Tetra Tech 2012). Still other consultants have reported that CALUX produced slightly lower dioxin TEQ values in comparison to Method 8290 for soil with relatively low concentration of dioxins in soil (e.g., <50 ng/kg).

While the correlation of the CALUX test with the GC/MS data is somewhat low, the conservative nature of the CALUX test at concentrations above HDOH action levels supports its use as screening tool to estimate maximum levels of TEQ dioxins in soil. The consistency of the results suggests that the differences are more than random subsampling and laboratory error. This suggests that a pilot study on the use of CALUX methods and development of calibration curves prior to full-scale employment would be advisable.

Method: This method is a bio-analytical screening procedure for dioxin-like compounds in soils/sediments. This method is based on the ability of dioxin and related chemicals to activate the Ah receptor (AhR), a chemical-responsive DNA binding protein that is responsible for producing the toxic and biological effects of these chemicals. This method is a relatively rapid screening method capable of estimating the TEQs concentration for dioxin-like chemicals in a sample. A sample of soil is extracted in an organic solvent and fractionated through the sample processing procedure. An extract that contains the halogenated dioxins/furans is separated from an extract containing the halogenated biphenyls. These extracts are applied to monolayers of H1L6.1c3 cells and the amount of luciferase induction is measured after 20 to 24 hours. A standard dilution series of 2,3,7,8-TCDD is included on each plate of cells. Estimation of dioxin/2,3,7,8-TCDD-like TEQ activity present in the sample extract is performed by extrapolation to the 2,3,7,8-TCDD standard curve by least squares estimates with the 4 parameter Hill Equation. There are three modes by which the DIPS-CALUX bioassay is performed. These are the screening mode with historical recovery, screening mode surrogate recovery, and the semi-quantitative mode.

Data Use: Screening.

Target Analytes: PCDD/PCDFs in soil; a sample size of 2-10 g will typically give a detection limit of less than1 pg/g.

Advantages:

• Rapid testing of samples and reduced cost in comparison to Methods 8280 or 8290.
• Direct reporting of TEQ dioxin concentration avoids need to adjust results with respect to congener-specific TEFs.

Limitations:

• Small mass of soil tested (typically 5-10g).
• Field studies suggest overestimation of TEQ dioxins in comparison to GC/MS methods, especially at concentrations approaching or exceeding HDOH EALs;
• Samples expected to have extremely high levels of PAHs should be subjected to an additional cleanup step.
• Other contaminants in soil and sample extracts can be cytotoxic and impose a positive bias on the test (monitored as part of the method).
• Sample processing and cleanup procedures limit field use of the kits, although use in a laboratory setting can reduce costs in comparison to GC/MS methods.

HEER Office recommendations: The HEER Office recommends that dioxin levels be confirmed on 10% of the samples using laboratory GC/MS analyses (but at least 3 samples, whichever is greater). The GC/MS analyses should be conducted on samples with the highest-reported, bioassay TEQ dioxins results.

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Figure 8-8 PID for VOC screening

Method: A sample of soil is collected with minimal disturbance to minimize loss of volatile constituents using either a modified plastic syringe or commercially-available coring devices intended for this purpose. The sample is placed in a glass vial with organic-free reagent water, shaken, and a photoionization detector (PID) is used to measure the volatile organics found in the headspace over the sample/water mixture. This method may be especially suitable for screening of low levels of chlorinated solvents in soil. Refer also to field methods described for petroleum in soil in Subsection 8.4.2.

This method is strictly a screening procedure for estimating the total concentration of VOCs in soil and solid samples. This method can be used to estimate the relative concentration of VOCs in soil at a site prior to submittal to a laboratory and assist in the selection of low- or high-level analytical procedures at the laboratory (Hewitt and Lukash 1999). This can help ensure that adequate sensitivity can be achieved, while providing reasonable protection against overloading the analytical instrumentation used in quantitative purge-and-trap or headspace analyses. Use of this procedure may provide cost savings by minimizing the total number of aliquots of each sample that have to be collected for analysis by such quantitative laboratory-based techniques. Screening data can be compared to data for previously prepared, spiked soil standards from the site to estimate the concentration of VOC samples. The results of this screening procedure can also be used to guide other sample collection activities.

Data Use: Screening only.

Target Analytes: This method provides an estimate of the total concentration of volatile organics in soil. The method recommends using a standard at 200 ppb and using this standard to classify sample readings as “low” (below 200 ppb) or “high” (above 200 ppb).

Advantages: Samples can be analyzed in 5 minutes. Equipment is portable and battery operated. Sample analysis is cost effective.

Limitations:

• Small mass of soil tested (e.g., 5 grams);
• The type of volatile organics at the site must be known in advance and must be detectable by the PID. While PID responses to halogenated volatiles and aromatics may be fairly similar between compounds, the PID response to alkanes may be lower by an order of magnitude or more.
• As a screening method, this procedure is subject to a wide variety of potential interferences.
• False positives may occur if the PID is exposed to motor vehicle exhaust, solvents used for decontamination, or other sources of volatiles.

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Figure 8-9 Container setup for headspace screening (Hewitt and Lukash, 1999)

HEER Office recommendations: Headspace screening for chlorinated solvents in soil should be performed as specified in this method. Samples for VOC analysis should be collected immediately after the surface to be sampled has been exposed to the atmosphere (Hewitt and Lukash 1999). This includes samples both for screening and subsequent laboratory comparison analyses. The native structure of the material being sampled should experience minimal disaggregation during the collection and transfer process. The collection and transfer process should take less than 30 seconds and the sample weight is approximately (10 +2 g). The method specified sample container is shown above.

Immediately prior to analysis the vial should be hand shaken for 10-15 seconds for complete dispersion.

The most effective collection and handling protocols include either (a) the on-site, rapid transfer of discrete samples with a small coring tool to a hermetically sealable vessel that either already contains the appropriate dispersion/extractant solution or to which a solution can be added by puncturing the septum after a short period of storage (2 days at 4 degrees C) or (b) obtaining and temporarily storing (2 days at 4 degrees C) a sample in an EnCore sampler before transferring it to an appropriately prepared vessel.

Plastic bags or cores with plastic/Teflon on their end caps are not an acceptable substitution for the aforementioned sample collection methodology. Today it is recognized that past VOC sample collection and handling guidance often resulted in greater than 90 percent loss of VOCs from soil samples prior to laboratory analysis (Hewitt and Lukash, 1999).

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Figure 8-10 Pesticide immunoassay test kit components

Method: The method is performed using an extract of a soil sample. Filtered extracts may be stored cold, in the dark. An aliquot of the extract and an enzyme-chlordane conjugate reagent are added to immobilized chlordane antibody. The enzyme-chlordane conjugate “competes” with chlordane present in the sample for binding to chlordane antibody. The enzyme-chlordane conjugate bound to the chlordane antibody then catalyzes a colorless substrate to a colored product. The test is interpreted by comparing the color produced by a sample to the response produced by a reference reaction.

Data Use: Screening.

Target Analytes: Method 4041 is a procedure for screening soils to determine whether technical chlordane (chlordane isomers, endrin, endosulfan 1 and II, dieldrin and heptachlor) is present at concentrations above 20, 100 or 600 μg/kg. This analyte list is consistent with the HEER Office recommendation to evaluate total chlordane (see Subsection 9.1.3.3).

Advantages: Samples can be analyzed quickly and on-site. Most test kits require minimal training and are portable with battery-operated components. Sample analysis can be cost-effective.

Limitations: Compounds that are chemically similar may cause a positive test (false positive) for chlordane. In particular lower concentrations of aldrin and higher levels of toxaphene can cause a positive interpretation.

HEER Office recommendations: The HEER Office recommends an initial site-specific evaluation of this method. Multi Increment or equivalent sample data and laboratory comparison samples required for final decision making purposes. If compounds known to cause false positives are also present at the site, this method may not be appropriate.

Method: The method is performed using an extract of a soil sample. Filtered extracts may be stored cold, in the dark. An aliquot of the extract and an enzyme-DDT conjugate reagent are added to immobilized DDT antibody. The enzyme-DDT conjugate “competes” with DDT present in the sample for binding to DDT antibody. The enzyme-DDT conjugate bound to the DDT antibody then catalyzes a colorless substrate to a colored product. The test is interpreted by comparing the color produced by a sample to the response produced by a reference reaction.

Data Use: Screening.

Target Analytes: Method 4042 is a procedure for screening soils to determine whether 1,1,1-trichloro-2,2-bis(4-chlorophenyl) ethane (DDT) (CAS Registry 50-29-3) and its breakdown products (DDD, DDE, and DDA) are present at concentrations above 0.2, 1.0 or 10 mg/kg. Method 4042 provides an estimate for the sum of concentrations of DDT and daughter compounds by comparison against standards.

Advantages: Samples can be analyzed quickly and on-site. Most test kits require minimal training and are portable with battery-operated components. Sample analysis can be cost-effective.

Limitations: Compounds that are chemically similar may cause a positive test (false positive) for DDT and its daughter products. In particular low concentrations of chloropropylate, chlorobenzilate, and dicofol can cause a positive interpretation.

HEER Office recommendations: The HEER Office recommends an initial site-specific evaluation of this method. Multi Increment or equivalent sample data and laboratory comparison data required for final decision making purposes. If compounds known to cause false positives are also present at the site, this method may not be appropriate.

Method: The method is performed using an extract of a soil sample. Filtered extracts may be stored cold, in the dark. An aliquot of the extract and an enzyme-toxaphene conjugate reagent are added to an immobilized toxaphene antibody. The enzyme-toxaphene conjugate “competes” with toxaphene present in the sample for binding to the immobilized toxaphene antibody. The enzyme-toxaphene conjugate bound to the toxaphene antibody then catalyzes a colorless substrate to a colored product. The test is interpreted by comparing the color produced by a sample to the response produced by a reference reaction.

Data Use: Screening.

Target Analytes: Method 4040 is a procedure for screening soils to determine whether toxaphene (CAS Registry 8001-35-2) is present at concentrations above 0.5 μg/g.

Advantages: Samples can be analyzed quickly and on-site. Most test kits require minimal training and are portable with battery-operated components. Sample analysis can be cost-effective.

Limitations: Compounds that are chemically similar may cause a positive test (false positive) for toxaphene. In particular low concentrations of endrin, endosulfan I and II, dieldrin, and heptachlor can cause a positive interpretation.

HEER Office recommendations: The HEER Office recommends an initial site-specific evaluation of this screening method for each project. If compounds known to cause false positives are also present at the site, this method may not be appropriate. Laboratory comparison samples are required for final decision making.

Method: The method is performed using an extract of a soil sample, or directly on an aqueous sample. Filtered extracts may be stored cold, in the dark. An aliquot of the aqueous sample or extract and an enzyme-2,4-D conjugate reagent are added to immobilized 2,4-D antibody. The enzyme-2,4-D conjugate “competes” with 2,4-D present in the sample for binding to 2,4-D antibody. The enzyme-2,4-D conjugate bound to the 2,4-D antibody then catalyzes a colorless substrate to a colored product. The test is interpreted by comparing the color produced by a sample to the response produced by a reference reaction.

Data Use: Screening.

Target Analytes: Method 4015 is a procedure for screening soils and aqueous matrices to determine whether 2,4-dichlorophenoxyacetic acid (2,4-D) (CAS Registry 94-75-7) is likely to be present at concentrations above 0.1, 0.5, 1.0 or 5.0 mg/kg in soil, and 10 μg/L in water (ground water monitoring).

Advantages: Samples can be analyzed quickly and on-site. Most test kits require minimal training and are portable with battery-operated components. Sample analysis ican be cost-effective.

Limitations: Compounds that are chemically similar may cause a positive test (false positive) for 2,4-D. In general higher concentrations of chemically similar compounds are necessary to generate false positives and thus there are not significant interferences with this method.

HEER Office recommendations: The HEER Office recommends an initial site-specific evaluation of this method. Multi-increment or equivalent sample data and laboratory comparison data are required for final decision making purposes.

Method: This method uses a competitive immunoassay for the quantitative determination in water of triazine herbicides as atrazine. The method is performed using an aliquot of the water sample and an enzyme-atrazine conjugate reagent, which are added to an immobilized atrazine antibody. The enzyme-atrazine conjugate “competes” with triazine herbicides present in the sample for binding to the immobilized atrazine antibody. The enzyme-atrazine conjugate bound to the atrazine antibody then catalyzes a colorless substrate to a colored product. The test is interpreted by comparing the color produced by a sample to the response produced by a reference reaction.

Data Use: Screening.

Target Analytes: Method 4670 is a procedure for screening water with an optimal quantification limit of 0.03 μg/L for drinking water samples. The actual method sensitivity may be highly dependent on the kit used and sample matrix and the 0.03 μg/L lower detection limit may not always be achievable.

Advantages: Samples can be analyzed quickly and on-site. Most test kits require minimal training and are portable with battery-operated components. Sample analysis can be cost-effective.

Limitations: Compounds that are chemically similar may cause a positive test (false positive) for triazine herbicides. This cross-reactivity varies between different manufacturers and should be carefully evaluated for each project. Additionally, because this method quantifies triazine herbicides as atrazine, the response for the different compounds also varies between different manufacturers and also needs to be carefully evaluated for each project.

HEER Office recommendations: The HEER Office recommends an initial site-specific evaluation of this screening method for each project. If compounds known to cause false positives are also present at the site, this method and/or specific kit for this method may not be appropriate. Laboratory comparison data is required for final decision making purposes.

Method: Method 4010A is a procedure for screening solids such as soil and sludge and aqueous media such as wastewater and leachate for pentachlorophenol (PCP) (CAS Registry No. 87-86-5). The method is performed using a water sample or an extract of a water sample. The sample/extract and an enzyme conjugate reagent are added to immobilized antibody. The enzyme conjugate “competes” with PCP present in the sample for binding to immobilized anti-PCP antibody. The test is interpreted by comparing the response produced by testing a sample to the response produced by testing standard(s) simultaneously.

Data Use: Screening.

Target Analytes: Method 4010A is recommended for screening samples to determine whether PCP is likely to be present at defined concentrations (i.e., kits are available which give positive results at 0.005 mg/L for aqueous samples, and at 0.5, 10 or 100 mg/kg in soil samples).

Advantages: Samples can be analyzed quickly and on-site. Most test kits require minimal training and are portable with battery-operated components. Sample analysis can be cost-effective.

Limitations:: Compounds that are chemically similar may cause a positive test (false positive) for PCP. In particular lower concentrations of 2,4,6-trichlorophenol and 2,3,5,6-tetrachlorophenol can cause a positive interpretation.

HEER Office recommendations: The HEER Office recommends an initial site-specific evaluation of this method. Multi Increment or equivalent sample data and laboratory comparison data are required for final decision making purposes. If compounds known to cause false positives are also present at the site, this method may not be appropriate.

Method: The method was developed for wood treatment sites where PCP is the principal contaminant and other wood treatment chemicals, such as fuel oil and creosote are present. PCP is extracted from soil using methanol. An aliquot of the filtered methanol extract is added to acidified HPLC-grade water and the mixture is loaded onto a solid-phase extraction (SPE) column and eluted with hexane. The hexane eluate is mixed with basic water and is shaken. The aqueous solution is poured into a vial containing acidic water, octane, and cobalt chloride to facilitate separation. The mixture is shaken and allowed to separate. Approximately half of the octane is removed and added to a vial containing sodium sulfate. An aliquot of the octane is added to the vial containing the Quick Test® Reagent in an isopropyl alcohol solution. The mixture is placed in a plastic cuvette, mixed, and capped. The concentration of the PCP is determined using a dedicated colorimeter with the UV light exposure set at 260 nm.

Data Use: Screening.

Target Analytes: This method is recommended for analyzing soil samples to determine whether PCP is present at concentrations above 1.5 mg/kg. This method provides for the quantification of PCP relative to a three-point standard curve over a calibration range of 2 – 90 ppm.

Advantages: Samples can be analyzed quickly and on-site. Most test kits require minimal training and are portable with battery-operated components. Sample analysis can be cost-effective.

Limitations:

• Test reagents are highly sensitive to UV and have to be stored and used away from direct or indirect sunlight.
• The reagent can deteriorate slowly (based on post-exposure absorbance) but remains useful at 40 °C for up to 50 days. Deterioration at 60 °C occurred almost immediately, and post-exposure absorbance was significantly lower after 7 days. The reagent has been tested at 25 °C and remained stable for 4 months at that temperature.
• Compounds that are chemically similar may cause a positive test (false positive) for PCP; however, the clean-up steps in this method do eliminate most of this cross-reactivity and should not significantly impact this method.

HEER Office recommendations: The HEER Office recommends an initial site-specific evaluation of this method. Multi Increment or equivalent sample data and laboratory comparison data are required for final decision making purposes.

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Figure 8-11 Explosives immunoassay kit and explosives sample analysis using an immunoassay kit.

Method: The method is performed using an extract of a soil sample. Samples and an enzyme-trinitrotoluene (TNT) conjugate reagent are added to an immobilized TNT antibody. The enzyme-TNT conjugate “competes” with TNT present in the sample for binding to the immobilized TNT antibody. The enzyme-TNT conjugate bound to the TNT antibody then catalyzes a colorless substrate to a colored product. The test is interpreted by comparing the color produced by a sample to the response produced by a reference reaction.

Data Use: Screening.

Target Analytes: Method 4050 is a procedure for screening soil samples to determine when TNT (CAS No. 118-96-7) is present at concentrations above 0.5 mg/kg.

Advantages: Samples can be analyzed quickly and on-site. Most test kits require minimal training and are portable with battery-operated components. Sample analysis can be cost-effective.

Limitations: Compounds that are chemically similar may cause a positive test (false positive) for TNT. In particular lower concentrations of tetryl, 1,3,5-trinitrobenzene, and 2-amino-4,6-dinitrotoluene can cause a positive interpretation.

HEER Office recommendations: The HEER Office recommends an initial site-specific evaluation of this screening method for each project. If compounds known to cause false positives are also present at the site, this method may not be appropriate. Multi Increment or equivalent sample data and laboratory comparison samples are required for final decision making purposes.

Method: The method is performed using an extract of a soil sample. Samples and an enzyme conjugate reagent are added to immobilized hexahydro-1,3,5-trinitro-1,3,5-triazine (RDX) antibody. The enzyme-RDX conjugate “competes” with RDX present in the sample for binding to an immobilized RDX antibody. The enzyme-RDX conjugate bound to the antibody then catalyzes a colorless substrate to a colored product. The test is interpreted by comparing the color produced by a sample to the response produced by a reference reaction.

Data Use: Screening.

Target Analytes: Method 4051 is a procedure for screening soils to determine when RDX (CAS No. 121-82-4) is present at concentrations above 0.5 mg/kg.

Advantages: Samples can be analyzed quickly and on-site. Most test kits require minimal training and are portable with battery-operated components. Sample analysis can be cost-effective.

Limitations: Compounds that are chemically similar may cause a positive test (false positive) for RDX. In general higher concentrations of chemically similar compounds are necessary to generate false positives and thus there are not significant interferences with this method.

HEER Office recommendations: The HEER Office recommends an initial site-specific evaluation of this screening method for each project. Multi Increment or equivalent sample data and laboratory comparison samples are required for final decision making purposes.

Method: The method is performed using an extract of a soil sample. The sample is treated with color-change reagents and is read in a portable spectrophotometer. The colorimetric nature of the test is based on the visual detection of the reaction product that is formed when polynitroaromatic compounds react with acetone by ketone substitution in the presence of a base. This substitution product is measured at 540 nm using a spectrophotometer. The concentration of 2,4,6-trinitrotoluene (TNT) and closely related nitroaromatic compounds (2,4-dinitrotoluene, 2,6-dinitrotoluene, and 1,3,5-trinitrobenzene) in an unknown sample is determined by evaluating the intensity of the color that is developed.

Data Use: Screening.

Target Analytes: Method 8515 is a procedure for screening soil samples to determine when TNT (CAS No. 118-96-7) is present at concentrations above 1 ppm. The test also has similar reactivity to 2,4-dinitrotoluene, 2,6-dinitrotoluene, and 1,3,5-trinitrobenzene.

Advantages: Samples can be analyzed quickly and on-site. Most test kits require minimal training and are portable with battery-operated components. Sample analysis can be cost-effective.

Limitations: This test has similar reactivity for TNT as well as 2,4-dinitrotoluene, 2,6-dinitrotoluene, and 1,3,5-trinitrobenzene. Results from this test should take this fact into consideration.

HEER Office recommendations: The HEER Office recommends an initial site-specific evaluation of this screening method for each project. Multi Increment or equivalent sample data and laboratory comparison samples are required for final decision making purposes.

Limitations:

• The operation of the fluorescence system takes considerable experience. It takes many days and numerous projects to become familiar with the operation of the technology. Operation of the technologies is provided as services by their respective vendors for this reason.
• Although these sensors provide information regarding the relative degree of contamination that closely matches reference method data, little direct, quantitative correlation has been found to individual or classes of petroleum compounds.
• The cost of the large, truck-mounted versions of these systems may be prohibitive for small-scale projects. However, recent advancements in the delivery systems and laser electronics are making fluorescence systems capable of tackling almost any size job more economically.
• Some maintenance of the CPT tools and the LIF sensors is required, and breakdowns can be expected on long-term projects. For example, downtime due to breakage of fiber optic cables and push rods, fogging of the sapphire window, and problems with the grout pump or decontamination unit may occur.
• These systems can only be used where direct push is feasible, such as in unconsolidated sediments. The sensors are limited to a depth of 50 meters because of attenuation in the optical fiber umbilical cord.
• Minerals such as calcite, naturally occurring organic matter, and man-made chemicals also can fluoresce, which may cause interference problems. Smearing and a memory effect on the sensor may occur when pushing through fine-grained sediments such as clays.

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Figure 8-12 Membrane Interface Probe with Conductivity Probe Tip

A MIP is a semi-quantitative field screening device that can detect VOCs in soil and sediment. It is used in conjunction with a direct-push platform (DPP), such as a CPT testing rig or a rig that uses a hydraulic or pneumatic hammer to drive the MIP to the depth of interest to collect samples of vaporized compounds. The probe captures the vapor sample, and a carrier gas transports the sample to the surface for analysis by a variety of field or laboratory analytical methods. Additional sensors may be added to the probe to facilitate soil logging and identify contaminant concentrations. The results produced by a MIP at any location are relative and subject to analytic verification.

MIP technology is capable of sampling VOCs and some SVOCs from subsurface soil in the vadose and saturated zones. It is typically used to characterize hydrocarbon or solvent contamination. Its ability to rapidly locate and identify contaminants reduces uncertainty in management decisions associated with costly cleanup projects, such as those commonly involving source zones of dense non-aqueous-phase liquid (DNAPL) and light non-aqueous-phase liquid (LNAPL). MIP technology uses heat to volatilize and mobilize contaminants for sampling. Heating the soil and/or groundwater adjacent to the MIP’s semi-permeable membrane volatilizes the VOCs, which then pass through the probe’s membrane and into a carrier gas for transportation to the ground surface.

The MIP consists of a small polymer (tetrafluoroethene) port, or membrane, that is permeable to gas but impermeable to liquid. The port is secured onto a steel block that also contains a resistive heater coil and a thermocouple, allowing the temperature of the membrane to be controlled and monitored. The heater coil heats the soil near the membrane to 80 to 125 ºC (160 to 232 ºF), which allows VOCs in the soil and groundwater to partition across the membrane in saturated or unsaturated soil. The subsurface temperature needs to be at or above the boiling point of the target compound(s). Nitrogen is the most commonly used carrier gas, but helium has been used in some applications. The carrier gas sweeps across the back of the membrane, entrains the VOC sample, and carries the VOC to the detection device located at the surface.

Typically, the MIP probe includes a tip that measures soil or water conductivity at a known distance below the membrane. The conductivity measurements can help correlate contamination to known soil stratigraphy. The probe conductivity measurements cannot identify the specific type of soil (based on grain size) distribution that is encountered unless the conductivity measurements can be compared to actual site soil core data. In the absence of on-site data, the MIP conductivity measurements identify changes in the soil’s electrical behavior that can be related to changes in stratigraphy or groundwater quality. Analytical devices commonly used with an MIP include gas chromatography (GC)-grade detectors (e.g., photo-ionization [PID], flame ionization [FID], electron capture [ECD], and dry electrolytic conductivity [DELCD] detectors) that establish the presence of VOC vapor, dissolved phase LNAPL, or DNAPL in soil. These detectors may be deployed singly or in line depending upon the site’s contamination. PIDs are best used for detecting aromatic compounds, such as BTEX (benzene, toluene, ethylbenzene, and xylene isomers). FIDs are used to detect petroleum hydrocarbons (straight and branched chain alkanes). ECDs and DELCDs are used to identify chlorinated hydrocarbons (e.g., PCE, TCE, dichloroethene, carbon tetrachloride).

Speciation of the contaminants can be accomplished either by collecting the off-gas on carbon or Tenax traps and subsequently desorbing the contaminants into a GC/mass spectrometer (MS), or by direct injection into an on-site ion-trap mass spectrometer (ITMS). Since the ITMS lacks a GC, its ability to resolve complex mixtures of contaminants is limited. See ASTM 2007b for a standard describing use of DPT for volatile contaminant logging with the MIP.

Advantages

• Real time data.
• Limited investigation derived waste.

Limitations

• MIPs provide screening-level data that need to be supplemented with analytical soil or groundwater data to fully support human health risk assessments or remediation decisions.
• Determining the depth at which the sample was taken when the sampler is in a near-continuous operating mode and the push rate is variable can be difficult. Compounds may be found in the subsurface for which the detectors were not calibrated.
• As with all direct push devices, MIP is only useful for deployment in unconsolidated matrices. Speciation with the ITMS can be problematic when the gas stream contains a complex mixture of chemicals. In many cases, the detection limit of MIP equipment for specific contaminants is above the detection limit required for human health risk assessment.
• ITMS-MIP overestimates contaminant concentrations for most vadose zone soils when compared with validation results, and it underestimates contaminant concentrations for clay-type vadose zone soils.

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Figure 8-13 Combustible Gas Indicator

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8.6.1 COMBUSTIBLE GAS INDICATOR (CGI)

This meter typically uses a platinum filament, which is heated by burning the combustible gas or vapor. The increase in heat is measured and reported as a percent of the lower explosive limit (%LEL). Generally if the gas is flammable, the Combustible Gas Indicator (CGI) reading is +50 percent when the meter is calibrated to hexane. The CGI has multiple sensitivities and thus can read a wide range of atmospheric levels on one meter. This meter operates only at normal oxygen levels and is also subject to electronic noise and is not very accurate at very low levels.

Advantages

• Measures the presence of combustible gases/vapors
• Range : 0 – 100 % of LEL (units are % of the LEL or ppm depending on the instrument brand used)

Limitations

• Catalytic sensor poisoning
• Relative response
• Does not indicate mists or dusts
• Must have normal oxygen content (generally at least 16 %) to provide valid readings

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Figure 8-14 Oxygen Meter

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8.6.2 OXYGEN METER

This instrument uses an electrochemical sensor to measure the partial pressure of oxygen levels in the air and converts that reading to oxygen concentration. A deficient oxygen atmosphere (<19.5 percent) can indicate displacement by another gas or consumption. An oxygen atmosphere with a surplus (>23.5 percent) can indicate another source of oxygen. Either situation is potentially life-threatening and hazardous. It is important to understand that the meter only considers the effect of oxygen itself and not the presence of other materials. Any deflection on the oxygen meter should be treated as an abnormal situation. Neutralizing and masking gases can affect the accuracy of this instrumentation.

Advantages

• Measures oxygen levels in the air

Limitations

• Neutralizing and masking gases

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Figure 8-15 Flame Ionization Detector

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8.6.3 FLAME IONIZATION DETECTOR (FID)

This meter has low detection levels for a broad number of organic compounds and has a self-adjusting span for known compounds. The FID ionizes compounds by burning them in a hydrogen flame. Operations on site may result in variable background levels of airborne compounds. Airborne compounds may be released from vehicles, blowing dust, material transfers, and so on. These sources can complicate monitoring of contaminant emissions during project tasks. Therefore, several upwind and pre-work measurements should be taken to assess contributions to airborne contamination by other potential sources. The instrument can also flame out at 10,000 ppm and above.

Advantages

• Low detection levels for many organic compounds
• Self-adjusting span for known organic compounds
• Ionizes compounds by burning them in hydrogen flame
• Can detect compounds with high ionization energy vapors (such as methane).

Limitations

• Can flame out at 10,000 PPM
• Multiple sensitivities
• Does not differentiate between compounds detected

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Figure 8-16 Photoionization Detector (MiniRAE)

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8.6.4 PHOTOIONIZATION DETECTOR (PID)

This instrument detects atmospheric contaminants by ionizing them with UV radiation and producing a current that is proportional to the number of released ions. A PID with a 10.6 electron volt (eV) lamp should be sufficient for measuring VOCs and can be used for monitoring activities. A PID can determine compounds at very low concentrations with little electronic noise; the typical range is 0.5 to 2,000 ppm. The instrument is self-adjusting for known compounds but is blind to many common gases (methane, for example). Operations on site may result in variable background levels of airborne compounds. Airborne compounds may be released from vehicles, blowing dust, material transfers, and so on. These sources can complicate monitoring of contaminant emissions during project tasks. Therefore, several upwind and pre-work measurements should be taken to assess contributions to airborne contamination by other potential sources. This instrument is not accurate at high levels.

Advantages

• Can detect many analytes and organic compounds at very low concentrations

Limitations

• Not accurate when analytes and compounds are present in the air at high concentrations
• Does not differentiate between compounds detected
• Does not detect acid gases (HCl, HNO₃)
• Does not detect PCBs
• Humidity reduces accuracy
• Dusts / Mists reduce accuracy
• Extreme heat and cold may affect instrument response
• Does not detect methane and other vapors with high ionization energy
• Multiple sensitivities (multiple electron volt [eV] lamps may be needed)