Applied and Environmental Soil Science

Volume 2012 (2012), Article ID 751956, 11 pages

doi:10.1155/2012/751956

Research Article

Quantitative Analysis of Total Petroleum Hydrocarbons in Soils: Comparison between Reflectance Spectroscopy and Solvent Extraction by 3 Certified Laboratories

Guy Schwartz,1,2,3 Eyal Ben-Dor,² and Gil Eshel⁴

¹Porter School of Environmental Studies, Tel-Aviv University, Tel-Aviv 69978, Israel

²Remote Sensing Laboratory, Tel-Aviv University, Tel-Aviv 69978, Israel

³Geography and Human Environment Department, Tel-Aviv University, P.O. Box 39040, Tel-Aviv 69978, Israel

⁴The Soil Erosion Research Station, Ruppin Institute, Emeck Hefer 40250, Israel

Received 9 January 2012; Revised 29 March 2012; Accepted 3 April 2012

Academic Editor: Jose Alexandre Melo Dematte

Copyright © 2012 Guy Schwartz et al. This is an open access article distributed under the Creative Commons Attribution License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original work is properly cited.

Abstract.

The commonly used analytic method for assessing total petroleum hydrocarbons (TPH) in soil, EPA method 418.1, is usually based on extraction with 1,1,2-trichlorotrifluoroethane (Freon 113) and FTIR spectroscopy of the extracted solvent. This method is widely used for initial site investigation, due to the relative low price per sample. It is known that the extraction efficiency varies depending on the extracting solvent and other sample properties. This study’s main goal was to evaluate reflectance spectroscopy as a tool for TPH assessment, as compared with three commercial certified laboratories using traditional methods. Large variations were found between the results of the three commercial laboratories, both internally (average deviation up to 20%), and between laboratories (average deviation up to 103%). Reflectance spectroscopy method was found be as good as the commercial laboratories in terms of accuracy and could be a viable field-screening tool that is rapid, environmental friendly, and cost effective.

1. Introduction

Among the chemicals that are relevant as environmental contaminants, petroleum hydrocarbons (PHC) are of particular significance. The widespread use of PHC for transportation, heating and industry has led to the release of these petroleum products into the environment through accidental spills, long-term leakage, or operational failures. Consequently, many soil and water areas are contaminated with PHC. PHC are well known to be neurotoxic to humans and animals. Several studies have been conducted in order to verify the effects of PHC on humans and animals [1–3]. For both the diagnosis of suspected areas and the possibility of controlling the rehabilitation process, there is a great need to measure correctly the amounts of PHC in soils.

Total petroleum hydrocarbons (TPH) is a commonly used gross parameter for quantifying environmental contamination originated by various PHC products such as fuels, oils, lubricants, waxes, and others [4]. Traditional wet chemistry methods for determining TPH level in soil samples is based on extracting the contaminant from the soil sample. The TPH level in the extracted solution is then determined by a gravimetric, FTIR, or GC measurement calibrated by an EPA calibration standard.

The TPH gross parameter is in use worldwide and facilitates an important stage of contaminated sites investigation; therefore, it is important to examine the effects of hydrocarbon type and soil properties on the extraction efficiency, as well as cross-lab repeatability.

The common method for assessing TPH in soil samples is based on a modified version of EPA method 418.1. This method is based on extraction with 1,1,2-Trichlorotrifluoroethane (Freon 113, GC 99.9%), although other extracting solvents are available (i.e., Carbon tetrachloride, N-Hexane, etc.). This method was originally introduced in 1978 [5] by the USEPA in order to assess TPH in waste water but was later adjusted in 1983 [6] for the assessment of TPH in soil samples. Newer methods are available for determining TPH in soil samples; these methods are based on extraction with other solvents and are usually followed by gas chromatograph analysis for THP determination. As these methods are more expensive, the EPA method 418.1 is in vast use as a screening tool [4, 7].

There are number of possible interactions between inorganic and organic soil components and organic pollutants, soil organic matter, and clays, having significant impact on solid-liquid extraction. Furthermore, the solvent extraction of compounds from soil or sludge samples is dependent on the moisture content in the soil [8]. There are some inherent problems with IR readings of the extracted solvent; all petroleum hydrocarbons do not respond equally to infrared analysis, and comparison of the unknown to a standard mixture may give results with high systematic errors [9]. The major problem with the adjusted EPA 418.1 method is that the extraction yields can be strongly matrix dependent, and the extraction method development and optimization may be quite complicated. These extraction-related problems mainly originate from the diversity of chemical and physical properties of petroleum hydrocarbons, which affect not only the solubility of hydrocarbons to the solvents, but also on the strength of analyte-soil matrix interactions, and therefore render the control of the extraction process of petroleum hydrocarbons from soil problematic.

In conclusion, it is clear that the adjusted EPA method 418.1 may overestimate TPH as a result of the following: (1) differences in infrared molar absorptivity for calibration standards and petroleum products; (2) detection of naturally occurring hydrocarbons; (3) infrared dispersion by mineral particles. Negative bias may also be introduced via (1) poor extraction efficiency of Freon-113 for high-molecular-weight hydrocarbons; (2) differences in molar absorptivity; (3) removal of five to six-ring alkylated aromatics during the silica gel cleanup procedure [10].

Quality assurance in the area of TPH determination is under developed and actually, except in few cases [11–13], there have not been any attempts to estimate the uncertainty related to the analytical procedure of TPH determination.

Taking in consideration all the possible biases that can occur during the adjusted EPA 418.1 method, as well as the fact that each laboratory uses somewhat different protocols and equipment for the extraction process and TPH determination; a methodic cross-laboratory evaluation is needed.

In addition to the traditional analytical chemistry methods used for measuring TPH in the soil samples, a new novel method based on reflectance spectroscopy was applied. Reflectance spectroscopy is commonly applied for quantitative analysis in many disciplines. This method consists of measuring the reflected electromagnetic energy from the soil samples in the VIS-NIR-SWIR region (350–2500 nm), and modeling this spectral data against samples with known concentration levels. Extracting the information about the soil attributes that is hidden within the spectral information, is done by using multivariate statistical techniques, also called chemometrics. Essentially, this involves regression techniques coupled with spectral preprocessing. A more detailed description of the spectral preprocessing and the chemometrics process as well as an overview of reflectance spectroscopy as a tool for monitoring contaminated soils can be found in a recent publication by the authors [7].

The spectral properties of hydrocarbons were identified at the late 1980s, although it was argued that these properties are visible at concentrations of 4% wt and above [14]. Several studies were conducted during the past 20 years in the field of PHC and reflectance spectroscopy (ie., [15–24]) that showed the potential of reflectance spectroscopy as being used as a tool for predicting TPH content. For taking a step forward in acceptance of this tool by the environmental protection authorities, a validation study that includes a comparison of the results of commercial laboratories analysis and reflectance spectroscopy performance is needed. Therefore, The goals of this study are (1) a comparison of the inner and interlaboratory TPH measuring capabilities, (2) general accuracy of the measured TPH levels as compared to the known TPH levels of the contaminated soil samples, and (3) Testing reflectance spectroscopy as a viable replacement for the traditional methods based on solvent extraction.

2. Materials and Methods

Three certified laboratories in Israel were selected for this study. Analogue soils typical to Israel were artificially contaminated with PHC and sent at the same time and in the same conditions to all laboratories. In addition, the samples underwent a new NIRS procedure that we developed in TAU in which reflectance spectroscopy is used to determine TPH level [7].

2.1. Soils and Hydrocarbons

Three soils were selected for this study (defined according to Israeli naming system [25] as well as the USDA key to soil taxonomy [26]): Loess (Typic Xerofluvent), Hamra (Typic Xerocherept), and Gromosol (Typic Chromoxerert). These soils represent a wide range of soil properties as described in Table 1 and are significantly differ from each other. The soils were collected from areas that were assumed to have no PHC contamination and were air-dried and sieved through a 2 mm sieve twice. The soils properties were determined by the traditional methods in soil science as follows: hydroscopic moisture content was determined by weight loss after 24 h at 105°C. pH level and electrical conductivity were determined with a laboratory bench top 86505 pH/Conductivity meter by M.R.C Ltd. in a 1 : 2 soil and DI water suspension (resp.) after reaching equilibrium (30 minutes). Specific surface area (SSA) was determined by the absorption of mono layer of ethylene glycol monoethyl ether (EGME) [27]. Particle size distributions were determined by Marvin Mastersizer 2000 following Eshel et al. methodology [28]. SOC, SIC, and Total N were determined by a flash CHN elemental analyzer (Thermo Scientific Flash 2000). The soils analogue contaminated samples were prepared by mixing a known weight of several PHC types including: octane fuel, diesel and kerosene with known quantities of soil. For making well-mixed low concentration samples, we initially mixed a batch of 98.5 gr of soil with 1.5 gr of the selected PHC; after mixing the initial batch, the batch was then mixed again with clean soil at three concentration levels. In order to minimize the loss of PHC components, we minimized exposure to open air as much as possible. Each sample was divided equally into 4 amber glass vials, capped with a PTFE lined cap, and kept at 4°C. Three of the vials were sent to the analytical laboratories for analysis, 1 vial was kept for reflectance spectroscopy analysis. Table 2 describes the samples contamination properties and presents the calculated concentration info.

Table 1: Major soil properties.

Israeli local

name
USDA classification
HM
Sand
Silt
Clay
SOC
SIC
Total N
pH¹
EC¹
SSA

%
volume %
g kg⁻¹
mS m⁻¹
m² g⁻¹

Loess
Typic xerofluvent
4.14
38.6
49.4
12
5.4
22.5
0.9
8.22
5.44
167

Hamra
Typic xerocherept
1.44
97.37
1.73
0.9
1.5
2.1
0.5
8.57
0.08
83

Gromosol
Typic chromoxerert
5.23
46.46
38.98
14.56
7.6
12.5
1.3
8.68
0.55
238

11 to 2 ratio.

Table 2: Soil samples calculated concentration, projected TPH, and laboratory TPH results.

Sample
Soil

name
Contaminant
Calculated concentration (ppm)
Projected     TPH
Spectroscopy     (TPH)
Lab A (TPH)
Lab B (TPH)
Lab C (TPH)

Min
Max
Avg
Min
Max
Avg
Min
Max
Avg

1
Hamra
None
0
0
411
6
8
7
10
10
10
10
10
10

2
Diesel
450
567
908
354
434
394
599
610
605
458
506
483

3
4500
5674
4617
4575
5288
4932
6179
6292
6236
3730
4480
4111

4
10500
13239
8693
8122
8175
8149
14534
15369
14952
9897
10217
10021

5
Kerosene
550
670
953
277
320
299
405
415
410
305
383
350

6
6000
7304
4871
5455
6039
5747
7441
7528
7485
3420
3814
3628

7
12000
14609
8567
8740
9608
9174
14078
14125
14102
9410
9880
9704

8
95% octane
600
365
511
39
43
41
52
66
59
47
56
51

9
5500
3348
1274
519
586
553
793
838
816
244
333
300

10
9500
5783
1800
1227
1816
1522
1142
2003
1573
260
312
279

11
Loess
None
0
0
10
9
9
9
10
10
10
10
15
12

12
Diesel
500
630
1378
252
275
264
615
625
620
483
510
498

13
2500
3152
2545
1139
2308
1724
3593
3601
3597
2816
3055
2936

14
9000
11348
6062
5984
7303
6644
12447
12958
12703
7970
8560
8313

15
Kerosene
400
487
909
128
145
137
345
354
350
210
255
236

16
4000
4870
3182
2606
3250
2928
4687
4698
4693
2145
2312
2219

17
11000
13391
6495
9435
9628
9532
13184
13411
13298
7264
7859
7533

18
95% octane
700
426
937
34
47
41
70
70
70
46
69
54

19
4500
2739
704
210
228
219
629
635
632
62
88
73

20
10000
6087
1100
1188
1193
1191
2674
3107
2891
578
629
601

21
Gromosol
None
0
0
655
6
6
6
10
10
10
78
110
91

22
Diesel
600
757
737
356
381
369
640
677
659
463
512
490

24
3500
4413
1419
2613
2917
2765
4441
4624
4533
2493
2706
2621

23
11000
13870
2376
11753
14593
13173
14705
14800
14753
10513
11219
10811

25
Kerosene
600
730
714
223
237
230
439
470
455
190
254
222

26
5000
6087
1728
3494
4169
3832
5588
5613
5601
1231
1376
1306

27
10000
12174
3320
5839
6209
6024
11245
11436
11341
7922
8510
8261

28
95% octane
500
304
739
20
20
20
51
62
57
10
10
10

29
5200
3165
1916
410
491
451
680
691
686
228
265
249

30
9000
5478
1885
958
1127
1043
1800
1852
1826
685
824
743

2.2. Extraction and TPH Measurement Method

The general methodology for the adjusted EPA 418.1 method is based on taking a representative soil sample (3–10 gr.), adding sodium sulfate (1–5 gr.) to absorb any water and adding an extracting solvent (usually Freon 113, 20–30 mL) to the mixture. This mixture is then kept in a sealed glass vial capped with a PTFE cap and placed in a sonic bath for assisting and hasting the extraction process (about 10–45 minutes). Silica gel is then added to the mixture to absorb any polar hydrocarbons (nonfuel-related soil organic matter and fatty acids), and the mixture is mixed well. The filtered extract is then measured in an FTIR spectrometer at 3.42 μm (some laboratories use other absorption peaks in the close region). A calibration curve is created by using the 418.1 EPA standard (consists of 31.5% isooctane, 35% hexadecane and 33.5% chlorobenzene) diluted in the same extracting solution at at least 3 concentrations. The absorption depth of the measured sample is then converted to TPH values by the calibration curve. As this method is an adjusted EPA method, it can vary slightly between analytical laboratories, depending on internal laboratory standards, procedures, and equipment. The three laboratories used for analyzing the samples prepared for this study are commercial laboratories, certified by the national laboratories certification authority, thus the exact procedure is confidential and not known to the authors, although the principal remains the same. All 30 contaminated samples prepared for this study as described above were sent to the three certified laboratories for chemical analysis determination of TPH levels, the results are summarized in Table 2.

2.3. IR Absorbance of Diesel, Kerosene, Octane 95, and 418.1 EPA Reference

PHC efficiency to absorb IR radiation depends on the PHC molecules structure. It was important to map these absorptions differences for the contaminants used in this study, relative to the 418.1 EPA reference that is usually used for TPH determination. Diesel, kerosene, octane 95, and the 418.1 EPA reference were mixed with Freon 113 at four different concentration levels each: ~50, ~100, ~150, and ~200 ppm. Each sample was then measured for its absorbance by a buck scientific 404 analyzer; the results are shown in Figure 1. Since the relation between the absorption and the concentration for each PHC is perfectly linear, (see Figure 1), the absorption was calculated for each PHC for the following concentrations: 50, 100, 150, 200, 250, 300, 350, 400, 450, 500 ppm. Each PHC was then plotted versus the 418.1 EPA reference as shown in Figure 2.

Figure 1: IR absorbance versus concentration (ppm).

Figure 2: Contaminant IR absorbance versus 418.1 EPA reference IR absorbance.

2.4. Conversion of Specific PHC to TPH

Due to the fact that laboratories give results in TPH which is a gross parameter based on the EPA standard that represents a mixture of several PHC, and our soil samples were contaminated by a specific PHC, we need to apply a conversion factor from the specific PHC to the relative gross parameter TPH as seen is Figure 2. This resulted “Projected TPH” value should represent the contamination level of the contaminated samples if the laboratory process was flawless, thus eliminating one major bias factor, which is the difference between IR absorbance efficiency of the 418.1 EPA standard, relative to the specific PHC we used to contaminate the soil as described in the previous section. The conversion equations to project the specific PHC to TPH values in this study (Figure 2) are:

(1)TPH (ppm) = Diesel (ppm) * 1.2609 + 0.0067,(2)TPH (ppm) = Kerosene (ppm) * 1.2174 + 0.0055,(3)TPH (ppm) = Octane 95% (ppm) * 0.6087 + 0.0039,

The calculated projected TPH values are shown in Table 2, and are used for the rest of this study instead of the original specific PHC levels.

2.5. Intralaboratory Consistency Factors

The contaminated soil samples from each laboratory separately were divided into three groups: low, medium, and high, by the known concentration level, regardless of soil type or contaminant. The intralaboratory consistency was evaluated by four factors.

(1)Average delta: the difference between maximum TPH value and minimum TPH value of each sample in that group, followed by averaging the results of all the samples in that group.(2)Average deviation: the difference between maximum TPH value and minimum TPH value of each sample in that group, then divided by the average TPH value for that sample, thus normalizing the results. Finally the normalized results of all samples were averaged for all samples in each group.(3)Maximum delta: same as average delta, but instead of averaging the results for each group, only the maximum value was selected, portraying the “worst case scenario.”(4)Maximum deviation: same as average deviation, but instead of averaging the results for each group, only the maximum value was selected, portraying the “worst case scenario.”

Results are shown in Table 3.

Table 3: Intralab repetition statistics for low, medium, and high TPH levels.

Lab
A
B
C

TPH level (calculated)
AVG delta
AVG deviation
Max delta
Max deviation
AVG delta
AVG deviation
Max delta
Max deviation
AVG delta
AVG deviation
Max delta
Max deviation

Low

(400–600)
24
12%
80
32%
15
7%
37
24%
38
17%
78
40%

Medium (2500–6000)
473
20%
1169
68%
54
2%
183
6%
229
16%
750
35%

High (9000–12000)
712
13%
2840
39%
361
10%
861
55%
390
9%
706
18%

2.6. Interlaboratory Consistency Factors

The interlaboratory consistency factors were calculated in the same way the intrafactors were calculated, but instead of taking the samples from each laboratory separately, all samples from all laboratories were joined together, as if they came from the same laboratory. The same four factors: average delta, average deviation, maximum delta, and maximum deviation were calculated as described in the intralaboratory consistency factors section. Results are summarized in Table 4.

Table 4: Interlab repetition statistics for low, medium, and high TPH levels.

TPH level (calculated)
AVG delta
AVG deviation
Max delta
Max deviation

Low (400–600)
190
83%
373
199%

Medium (2500–6000)
2203
103%
4382
209%

High (9000–12000)
4564
90%
7247
178%

2.7. Spectroscopy TPH Measurements

The contaminated soil samples were measured according to TAU’s protocol [29] by an ASD Fieldspec pro instrument with an ASD contact probe 3 times, each consisting of 30 measurements that have been averaged; the 3 resulting spectra for each sample were averaged. The average spectrum for each sample was used to predict the TPH level by a PLS model based on several soil types and PHC types, predeveloped in the last few years by the authors. The modeling procedure included five types of soils, three types of PHCs at 50 concentration levels, yielding 750 laboratory prepared samples. An “all possibilities” approach was used for generating robust NIRS models. This approach includes the evaluation of many preprocessing techniques (SNV, MSC, smoothing, absorbance, first and second derivatives, and continuum removal), as well as PLS and ANN modeling methods (i.e., [7, 22, 30–33]).

2.8. General Accuracy

In order to evaluate the reliability of the reflectance spectroscopy method as compared to the common EPA 418.1 method as an environmental monitoring tool, the general accuracy of both methods had to be examined. General accuracy is an important parameter as it determines not only the intra- and interperformances of the laboratories but also portrays the ability of the laboratory to determine the actual contaminant concentration in the sample. General accuracy of TPH measurements done by both reflectance spectroscopy and analytical laboratories, was measured by the same previously mentioned factors used for inter and intra groups as shown in Table 5 (average delta, average deviation, maximum delta, and maximum deviation). The average delta was calculated for each group; by first calculating the delta for each sample in that group (average TPH value-projected TPH value) followed by averaging the results of all the samples in that group. The average deviation was calculated for each group by first calculating the delta for each sample in that group (average TPH value-projected TPH value), then dividing the result with the projected TPH value for that sample, thus normalizing the results. Finally the normalized results of all samples were averaged for each group. The maximum delta and maximum deviation were calculated in the same manner, but instead of averaging the results for each group, only the maximum value was selected portraying the “worst case scenario.”

Table 5: Accuracy of TPH determination by reflectance spectroscopy and three commercial laboratories.

Lab
Spectroscopy
A
B
C

TPH level (calculated)
AVG

delta
AVG deviation
Max

delta
Max deviation
AVG

delta
AVG deviation
Max

delta
Max deviation
AVG

delta
AVG deviation
Max

delta
Max deviation
AVG

delta
AVG deviation
Max delta
Max deviation

Low (400–600)
325
68%
747
143%
349
68%
500
93%
192
42%
356
84%
283
57%
508
97%

Medium (2500–6000)
2055
47%
4360
74%
1956
51%
2795
92%
1010
30%
2532
78%
2590
60%
4781
97%

High

(9000–12000)
6187
61%
11494
83%
4392
49%
6150
81%
1827
26%
4210
73%
4413
50%
5859
95%

3. Results and Discussion

Inner laboratory consistency seems very acceptable with results of under 20% average deviation for all 3 labs with lab B having the best consistency of under 10% deviation (Table 3). Although the average deviation is low for all laboratories, in some cases high deviation can occur, even up to 68% as can be seen in Table 3 (medium concentration samples, Lab A). The interlaboratory consistency on the other hand is far from satisfactory. Average interlaboratory deviation is between 83% and 103% and can even reach values of ~200% in some cases, that is: a Hamra sample contaminated with diesel (Sample 4, Table 2) yielded an average value of 8149 TPH from Lab A and 14952 TPH from Lab B. Both intra and interlaboratory average deviation are presented in Figure 3, performance of Lab A and Lab C are about similar, with better performances by Lab B. General accuracy was also not satisfactory as seen in Table 5, average deviation ranged from 26% up to 68%. Many of the accuracy errors are in measuring 95% octane fuel; this could be a result of loosing most of the contaminant during the extraction process due to the high volatility nature of this PHC. Performance of all laboratories, including the reflectance spectroscopy method, are almost identical as shown in Figure 4, with Lab B being the most accurate laboratory. Although accuracy was not satisfactory, a good correlation appears when plotting the reflectance spectroscopy and laboratories TPH results against the projected TPH results as demonstrated in Figures 5, 6, and 7. This shows that both the spectroscopy and the laboratories TPH results are consistent and are good predictors of the contamination levels. Because it is clear that 95% octane fuel is a problematic contaminant due to its high volatility, when we examine the results while ignoring the 95% octane contaminated samples, almost perfect correlation coefficient appear (Figures 8, 9, and 10). These correlations between the reflectance spectroscopy and the laboratories TPH results shows consistency of Lab B being always over estimating the projected TPH values, and the reflectance spectroscopy, Lab A and Lab C always under estimating the projected TPH values at almost the same level. As this phenomena being so consistent, it can be corrected by the correlation factors specific for each Laboratory. The result of this study confirms the hypothesis of large variations between laboratories and methods, even though they are properly certified by the authorities. It is interesting to note that with a precise approach, it is possible to account for these variations, correct and calibrate the results to represent the contamination levels accurately, thus enabling reliable comparable results. Reflectance spectroscopy was found to be as good as the traditional method employed by the commercial certified laboratories. Reflectance spectroscopy is a nondestructive method that can be used for rapid, simple, and cost effective TPH determination both in the laboratory and in the field. Moreover, the resent advances in imaging spectroscopy field could enable the adding of a new spatial dimension for site investigation, opening new frontiers in monitoring PHC contamination in soil.

Figure 3: Intra-/interlaboratory deviation.

Figure 4: Average and maximum deviation from projected TPH.

Figure 5: Hamra with all PHC types.

Figure 6: Loess with all PHC types.

Figure 7: Gromosol with all PHC types.

Figure 8: Hamra with diesel and kerosene.

Figure 9: Loess with diesel and kerosene.

Figure 10: Gromosol with diesel and kerosene.

4. Conclusion

While accuracy level is affected by various elements such as laboratory protocols, equipment and personnel, results remain very consistent and can be corrected when certain factors specific for each laboratory are employed. When a new batch of samples needs to be evaluated, a sample of clean soil similar to the same batch, contaminated with the 418.1 EPA standard at two levels can be added to the batch, thus helping to model the bias for this batch and to calibrate the results. Due to the problematic nature of measuring the 95% octane TPH levels, a PID (Photo Ionization Detector) instrument should be used to accompany each sample to help measure the volatile PHC. Reflectance Spectroscopy performed very well in this study (almost the same as Lab A and Lab C), and should be considered as a tool for field screening due to its very low cost per sample, easy operation, ability to work in field conditions, and the possibility of fast measurements and instant results. Reflectance spectroscopy is a nondestructive environmental friendly method; that when coupled with a PID device (for volatile PHC detection) could be used as an excellent screening tool in the field. When using reflectance spectroscopy coupled with PID, contaminated samples should not elude detection. In general the 418.1 EPA method alone should not be used to grant a “clean bill of health” to any contaminated site, but only as a screening and decision-making tool before more expensive methods are employed. It is strongly recommended that any certified laboratory and method will be improved by using a standard protocol suggested in this study, for calibrating the laboratory results to the real contamination level of the soil. Applying these protocols will assure both intra- and interaccurate, consistent, and comparable results.

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