Paper presented at 

Symposium on 

Cement and Concrete 

in the Global Environment 

March 10,1993 

O'Hare Marriott Hotel 

Chicago, IL 

LEACHABILITY OF 

SELECTED CHEMICAL ELEMENTS 

FROM CONCRETE 

Howard M. Kanare 

principal Scientist 

Chemical Services 

Presbury B. West 

Senior Scientist 

Materials Research and Consulting 

Construction Technology Laboratories, Inc. 

5420 Old Orchard Road 

Skokie, IL 60077-1030 

Phone 708.965.7500 

Fax 708.965.6541 
Kanare, H. M. and West, P. B.*, "Leachability of Selected Elements from Concrete," in 

Proc. Symposium on Cement and Concrete in the Global Environment March 1993, PCA. 

SUMMARY 

Eight portland cement concretes were made from four cements and two aggregates, one 

siliceous and one calcareous. A concrete cylinder from each was crushed according to U. S. 

Environmental Protection Agency SW-846 protocol and tested by the Toxicity Characteristic 

Leaching Procedure. In addition to eight elements specified in the Resource Conservation 

and Recovery Act - arsenic (As), barium @a), cadmium (Cd), chromium (Cr), lead (Pb), 

mercury (Hg), selenium (Se), and silver (Ag) - the concentrations of four other metals were 

also determined: antimony (Sb), beryllium (Be), nickel (Ni), and thallium (Tl). Analysis for 

most metals was performed by graphite furnace atomic absorption spectrophotometry to 

obtain the lowest possible detection limits consistent with sample compositions and analyte 

concentrations. Results indicate metal concentrations in leachate are all less than one-tenth 

RCRA regulatory limits, and many concentrations are below detection limits. Chromium 

TCLP cement values correlate with concrete leachate values while lead values do not. 

A second series of leaching tests was performed with deionized water in place of acetic acid 

solution. These tests are called "water leaching by TCLP protocol" in this paper. Four of the 

concretes representing both aggregates and two of the cements were tested by this procedure. 

Analysis of the concrete extracts was performed for the same twelve metal analytes. 

Concentrations of metals in water leachate are generally similar tor lower than 

concentrations in acid leachate. 

A third series of tests was performed on all eight concretes generally following ANSYNSF 

61 to simulate leaching with drinking-quality water as wouldccu in a municipal water 

supply system. Concentrations of As, Ba, Se, and Ag were nearly all below detection limits 

and well below NSF specification maxima. Concentrations of Cr, fluoride, and nitrate were 

all below NSF specification maxima. Despite precautions to work with high-puxity reagents 

and ultra-clean vessels, control samples showed Hg and Pb levels indicating probable 

contamination from the vessels used for soaking the concrete cylinders. This work points out 

how difficult it is to perform these tests when reporting limits are required in the sub-partsper-billion range. 

* principal Scientist and Senior Scientist, respectively, Construction Technology 

Laboratories, Inc., Skokie, IL 60077. 

1 
BACKGROUND 

This report examines two issues concerning the leachability of trace metals from concrete: 

leachability of crushed concxete specimens with dilute acetic acid and water following the 

U. S. EPA Toxicity Characteristic Leaching Procedure, and leachability from whole concrete 

specimens with synthetic drinking water following ANSVNSF 61 procedures. The purpose 

of this work is to determine if selected metallic elements are leached in significant quantities 

and to begin to understand the differences in results from leaching tests run on the same 

concretes according to different protocols. Issues include 1) whether leach tests on concrete 

batch components are additive and whether such tests can be used to predict the leachate 

composition of the hardened concrete; and 2) how does particle size affect leachate 

concentration. 

EXPERIMENTAL 

Cement 

Four cements were chosen from among the nearly 100 cements submitted for analysis and 

reported in the Portland Cement Association publication An Analysis of Selected Truce 

Metals in Cement and Kiln Dust (PCA Publication SPllO). These cements were chosen to 

represent a range of leachable metal concentrations, various cement manufacturing process 

types, and fuels used. Cements from participants 27,61,82, and 84 were selected and the 

data for total metals and TQ,P metals were obtained hm that report. Table 1 indicates the 

types of cements, manufacturing processes, raw materials, and fuels used to make these four 

cements. Tables 2 and 3 show the physical and chemical properties ofthe cements. Cement 

from participant 82 is an ASTM C 150 Type IA (air entraining) cement and the other three 

cements are either Type I or Type II. Cements 82 and 84 were made using supplemental 

waste fuels. 

Total and TCLP trace metal concentrations for the cements arehown in Tables 4 and 5. 

Figure 1 shows the concentrations of barium, chromium, and lead in acetic acid TCLP 

leachate from the four cements incomparison to the range and mean concentrations in all 

cements from the PCA study of U. S. and Canadian cements. 

Aggregates 

A mixed carbonats-siliceous sand from Elgin, Illinois was used for all eight concrete 

batches. Two kinds of coarse aggregate were selected from among materials fiequently used 

at CTL: siliceous coarse aggregate from Eau Claire, Wisconsin (a 60/40 ratio of two size 

fractions - 19 mm to 13 mm and 10 mm to 5 mm [3/4-in to 1D-in and 3/8-in to 3/16-in] 

and dolomitic coarse aggregate from Thornton, Illinois 19 mm topsize [3/4-inJ). The coarse 

and fine aggregates have well-known service histories and have been used for many years in 

research projects sponsored by the Portland Cement Association. TCLP tests were carried 

out on the sand and each aggregate fraction. The results of these TUP tests are shown 

Table 6. 

2 
Concrete Mixes 

Concrete mixes were designed to obtain roughly 30 Mpa (4500 psi) compressive strength 

with a water-cement ratio of 0.55. Coarse aggregate:sand ratio was 6040 and the cement 

content was 335 kg/m3 (564 lb/cu yd) for all concretes. Municipal (Skokie, Illinois) tap 

water was used without additional processing. Water content was kept constant in order to 

keep the weight percent cement in the concretes the same while the slump was allowed to 

vary. Concrete mix designs are shown in Table 7. Concretes made with Eau Claire 

aggregate were designated EC27, EC61, EC82, and EC84 and those with Thornton dolomite 

were designated TD27, TD61, TD82, and TD84 where the numbers indicated the participant 

number of the cements. For each batch of concrete, 0.02 m3 (3/4 cu ft) of concrete was 

mixed in a pan mixer, the air-content was obtained, and eight 75 x 150 mm (3 x 6 in) 

cylinders were cast in polypropylene cylinder molds (DesLauriers, Bellwood, IL) without 

release agent. Cylinders were consolidated by rodding except TD27 which required 

vibration. Three cylinders of each mix were tested at 28 days for compressive strength. 

Slump, air content, unit weight, and 28-day compressive strengths shown in Table 8. 

Concrete cylinders were cured at 23' C (73" F) in the polypropylene cylinder molds with 

low-density polyethylene snap-fit covers. Samples for TCLP (acid and water) were 

demolded at 60-70 days of age, immediately prior to crushing for the extraction tests. 

Samples for the ANSYNSF 61 drinking water tests were used at 16 months of age. 

LEACHING PROCEDURES 

Sample Processing 

Each cylinder was demolded and broken into chunks with a steel hammer. These chunks 

were passed through a jaw crusher (BICO-Braun, Burbank, California) with hardened steel 

jaws set to produce particles mostly less than 9.5 mm (3/8 in). The crushed samples were 

passed through a brass 9.5 mm sieve. 

The question is often asked whether crushing and grinding contaminates samples with metals 

from the processing equipment such as jaw crushers, disc pulverizers, or swing mills. Data 

from a project using clinker give some insight into possible contamination in the processing. 

A sample of a relatively dense portland cement clinker was passed three times through the 

steel-plate jaw crusher (BICO-Braun, Burbank, CA) then ground with a ceramic mortar and 

pestle to pass a 150 pm (No. 100 U. S. Standard) sieve. A control sample of clinker was 

processed by grinding with a ceramic mortar and pestle to the same fineness. Flame AAS 

analysis for nitric acid-soluble nickel and chromium indicated small increases due t6 the jaw 

crusher processing (71.9 vs. 75.8 mag Cr and 15.1 vs 16.1 mg/kg Ni). For comparison, 

chrome alloy disk pulverizer plates (Model UA-2000, BICO-Braun, Burbank, CA) 

substantially increased chromium and nickel concentrations (71.9 vs. 166.3 mag Cr and 

15.1 vs 22.2 mag Ni). Milling 30 sec in a tungsten carbide swing mill (W. Bleuler, 

Zollikon; container Cat. no. 8504 from Spex Industries, Edison, New Jersey) did not 

contribute significant iron, nickel, or chromium, although cobalt increased (6.6 vs. 11.3 

3 
mg/kg). We m not aware of a practical processing method that would eliminate all metal 

contact and permit reduction of concrete cylinders to 9.5 mm (3R-h) size. 

TCLP (Acetlc Acid) 

EPA Method 131 1 was followed. For each crushed conmte sample, 100 g was weighed 

into a 2 L polypropylene smw-cap jar and 2000 g dilute acetic acid @H 2.88k0.05) was 

added. The jars were capped and tumbled in a four-bottle rotary agitation apparatus 

(Analytical Testing and Consulting Services Model DC-20, Warrington, Pennsylvania) at 30 

rpm for 18 hr at 23' C (73' F). Leachate was suction filtered thorough glass-fiber fdters 

(Whatman GF/F) and transferred to polyethylene bottles. The pH of each solution was 

recorded. The filtered leachates we= acidified to pH 4 with nitric acid 

TCLP (Water) 

The procedure presented above was followed using ASTM D 1193 Type I water instead of 

dilute acetic acid. 

Analysis 

Samples were digested and analyzed according to EPA SW-846 methods by atomic 

absorption spectrophotometry. The methods followed procedures described in the PCA 

cement and kiln dust report (SP110). 

RESULTS OF TCLP TESTS 

Estimates of Potential Metal Concentrations in Leachate 

Two estimates of potential metals concentrations in leachate were obtained by using the 

cement TUP result in one case (called the minimum estimate) and using the cement total 

metals result in the other case (called the maximum estimate). These results were combined 

with TUP results from the aggregates. If the TCLP results are additive, their sum should be 

a reasonable estimate of concentrations in the concrete leachate. 

The minimum estimate was obtained after first calculating for each metal the contribution 

from the cemento the potential leachate concentration using the weight fraction of cement in 

the concrete (0.1397) 'times the cement TCLP value for each analyte. This value was then 

added to the weighted sum of contributions from sand (3 1.19% of FA TUP) and from 

coarse aggregate (47.15% of CA TCLP) to give the minimum estimate. This value may be 

similar to actual leaching data if TCLP results are additive. As an example here is the 

calculation of the minimum estimate for barium inthe TCLP extract of concrete TD61: 

(0.1397 x 0.93)+(0.3119 x 0.33)+(0.4715 X 0.16) = 0.130+0.103+0.075 = 0.31 mg/L 

The maximum estimate was obtained after first calculating for each metal the maximum 

contribution from the cement to the potential leachate concentration using the weight fraction 

of cement in the concrete (0.1397) times the total metal in cement. This value was then added 

to the weighted sum of the contributions from sand (31.19% of FA TCLP) and from coarse 

aggregate (47.15% of CA TCLP) to give the maximum estimate. This value would occur if 

all of the metal analyte contained in the cement contributed to the concrete TUP result. As 

4 
an example here is the calculation of the maximum estimate far barium in the TUP extract of 

concrete TD61: 

(0.1397 x 8.15)+(0.3119 x 0.33)+(0.4715 x 0.16) = 0.139+0.103+0.075 = 1.32 mg/L 

Leachlng Results 

The TCLP (acid) concrete data are shown in Table 9. The concentrations of 12 metals were 

determined in leachates from 8 concretes producing 96 individual measurements; fifty of 

those results are below detection limits. For the individual metals analyses of the concrete 

TCLP (acetic acid) extract, all results for arsenic, beryllium, and selenium are below 

detection limits and six of the eight concrete leachates for antimony, cadmium, and thallium 

are below detection limits. For the remaining six metals, the leachate concentrations are 

below detection limits for two of eight results for mercury and nickel ; one of eight results is 

below detection limits for each of the rest of the metals. Normalized concentrations of these 

six metals in the eight concrete TCLP extracts are presented in Figwe 2. The eight results 

that fall below detection limits are shown at the detection limits. Concentrations are 

normalized to the individual RCRA limit for each metal and plotted on a logarithmic scale. 

The plot indicates all results are less than Moth the RCRA limits. Chromium and silver 

normalized concentrations (with one exception ) are between l/lOth and 1/1OOth of their 

RCRA limits. Most of the normalized concentrations for barium, lead, mercury, and nickel 

fall between 1/100th and 1/1OOOth of their respective RCRA limits. 

Comparison of TCLP (acid) and TCLP (water) 

The TCLP water data are shown in Table 10 and a comparison of selected acid versus water 

results is shown in Table 11. In most instances the TCLP acid leaching result falls between 

the maximum and minimum estimate while the TCLP water leaching result falls near or 

below the minimum estimate. (See Figure 2a.) 

Relation Between Cement and Concrete 

Approximately 15% of the crushed concrete is not recovered after filtering and drying the 

TCLP (acid) residue. This corresponds to the amount of cement in the concrete batches. The 

recovered solids consist of aggregate with little or no cement paste adhering. Whether the 

metals remain in solution or precipitate and become trapped in the filter residue determines the 

measured concentrations. 

Much interest surrounds chromium and lead levels inleachates. Figure 3 indicates that TUP 

chromium from the cements is correlated (R4.92) with TCLP (acid) chromium from the 

concretes. Total chromium in the cements also correlates (R4.89) with TCLP (acid) 

chromium from the concretes (Figure 4). While leachable chromium from all eight concretes 

is less than one-tenth of the 5 mg/L RCRA limit, these correlations may be useful to cement 

producers monitoring potential leachable chromium. 

No relationship appears to exist between lead levels in cement and TCLP conmete values 

(Figures 5 and 6). 

5 
DRtNKlNG WATER LEACHING 

Eight 3 x 6 in concrete test cylinders were tested generally following procedms in 

ANSI/NSF 61-1991, 'Drinking Water System Components-Health Effects," The purpose 

of these tests is to simulate exposm of drinking water to the interior surface of concmte pipe 

as the water is transported in a municipal water distribution system. These tests consist of 

conditioning the specimen followed by exposure to simulated drinking water containing 

buffering, hardness, and chlorinating agents. 

Experimental 

A dedicated room maintained at 23-24' C (74-76" F) was prepared by draping 0.15-mm 

(6-mil) polyethylene sheets to enclose a space roughly 2.5 x 3 x 2.5 m (8 x 10 x 8 Et) to 

minimize airborne contamination. Tacky mats (Liberty Industries) were placed immediately 

inside and outside the door of the mom to trap particulates on workers feet. To assure 

sufficient supply of high-purity water, a water-polishing station (Barnstead Nanopure, dual 

Ultrapure cartridges) fed from service &ionizer cartridges was placed in the room. 

Each concrete cylinder was brushedwith a steel-bristle brush under cold tap water and rinsed 

with ASTM D 1193 Type II deionized water. Cylin&rs were handled throughout with latex 

surgical gloves. Each cylinder was placed in a 19 L (5-gal) FDA approved, white 

polyethylene bucket (Philips Container Co.)which had been previously washed with soap, 

rinsed with tap water, washed with acid, washed with base, rinsed with tap water, and rinsed 

with Type II water. 

Stock solutions of sodium bicarbonate (0.04 M), calcium chloride (0.04 M), and sodium 

hypochlorite (1.5 ma residual total chlorine) were prepared using ACS reagent grade 

chemicals and Type I water. Conditioning water at pH 8 was made from the stock solutions 

using 260 mL 0.04 M NaHCO3,26O mL 0.04 M CaC12,13.9 mL NaOC1, and Type I water 

to make 10.4 L. This volume gave a surface area to volume ratio of 43.7 cm2/L based on a 

910-mm (34) diameter pipe. 

Specimens were fist exposed to conditioning water/disinfecting solution containing 50 mg/L 

available chlorine. Subsequent exposures contained 2m& available chlorine. Specimens 

were immersed in the conditioning water for 12 days with a change of water every 24 hours, 

and for two additional days with no change of water. The conditioning water was decanted 

and specimens were immersed in pH 8 extraction water of the same concentration as the 

conditioning water, at 23-24" C (74-76" F) for 16 hr . 

Extract water samples were decanted into pre-cleaned 125 mL (4 oz) amber glass bdttles far 

mercury analysis and into 2 L (64 oz) polyethylene bottles for other analytes. Nitric acid 

(1 1 mL, Baker Instra-Analyzed, 70%) was added to stabilize the solutions for metals 

analysis at pH 4. Five mL potassium dichromate/nihic acid solution (25 mL 70% HNO3 

plus 0.068 g K2Cr2O7, diluted to 500 mL)was added to stabilize the solutions for mercury 

analysis. Samples were maintained at room temperatm until analysis. A separate sample of 

each extraction water was taken for nitrate analysis to which no stabilizing agent was added. 

6 
At CX'L, samples were analyzed by graphite furnace atomic absorption spectrophotometry 

according to EPA SW-846 methods for As, Ba, Cd, Cr, Pb, Se, and Ag. Mercury was 

analyzed by cold vapor AAS. Fluoride was determined by double standard additions using a 

selective ion electrode. Nitrate was determined using a colorimetric test kit (Hach NI-10). 

Sample volumes and instrumental settings were chosen to give reponing limits generally onetwentieth or less of the Drinking Water Standards. 

Split samples also were analyzed according to EPA SW-846 methods at TEI Analytical, 

Niles, Illinois, using GFAAS for As, Pb, and Se; inductively coupled plasma spectrometry 

for Ag, Ba, and Cd; and Hg by cold vapor AAS. Fluoride was determined by ion 

chromatography according to ASTM D 4327. Reporting limits at TEI were generally equal 

to or better than one-tenth of the Drinking Water Standards. 

Results and Discussion 

To be listed as acceptable under the ANSI/NSF 61 protocol, drinking water system 

components must produce leachates with analyte concentrations less than one tenth the U. S. 

EPA National Primary Drinking Water Standards. Results of analyses from CTL and TEI 

laboratories are shown in Table 12. For comparison, the relevant drinking water standards 

are shown following the laboratory results. (For a complete set of drinking water standards, 

contact the EPA Safe Drinking Water Hotline at 800-426-4791 Monday-Friday 8:30 am5 pm EST). 

Values for As, Cd, Se, and Ag are nearly all below reporting limits. Concrete extracts 

contained Ba and Cr at less than one-tenth the drinking water standards. 

One approach for comparing TCLP and ANSWSF 61 protocols is to normalize results 

based on surface area to volume (SAV) ratios. Sieve analysis of a TCLP (water) residue was 

used to calculate the surface area of the residual concrete particles, yielding a surface area of 

3440 cm2/100 g. (This calculation assumed spherical particles. Since most surface area is in 

the finest fraction, which contains nearly equant particles, this assumption is reasonable. 

However, surface roughness, cracks, and permeability were ignored. Thus, the calculated 

surface area is likely lower than the actual surface area) In 2 L of TCLP leachate this is an 

SAV ratio of 1720 cm2L. The ANSYNSF 61 tests used an SAV of 43.7 cm2L. The ratio 

of SAV- to SAVNsF is approximately 40:l. Dividing Cr TCLP (water) values by 40 yields 

results approximately eight times higher than the drinking water results, suggesting that 

permeability of the relatively small crushed concrete particles is responsible for some Cr 

leaching. 

Lead and mercury in one control sample were higher than in any of the leachates, suggesting 

contamination of at least one control solution. Mercury levels were 10-20 times higher than 

expected in tap water and drinking water controls. To investigate the source of lead and 

mercury in control samples, duplicate samples of water were collected in glass bottles 

containing the nitric acid-dichromate preservative described above, at thefinal water deionizer 

just before filling the polyethylene buckets. Additional samples were taken from a second 

7 
deionizer used in a different part of C2L"s chbistry laboratory. The samples were tested for 

mercury and lead by AAS, yielding the following xesults: 

Concentration, pg/L @pb) 

Hg Pb Lab:m rn mrn 

deionizer 1* 0.06 n/a q0.2 n/a 

deioniZer2* 0.03 n/a <0.3 n/a 

control I? 0.9 3.2 5.8 3 

control 2? 0.5 0.3 1.0 3 

tap water? 0.2 0.7 2.7 n/a 

*Mean of duplicate determinations. n/a = not analyzed 

mater analyzed after soaking in polyethylene buckets, with no concrete, for la1 hr. 

We believe that contamination from the polyethylene buckets (or less likely, airborne 

sources) caused the concentrations of mercury and lead in controls to exceed levels in the 

concrete leachates. According to State of Illinois reports, the municipal water supply used to 

make concrete should have contained less than 0.05 clg/L (ppb) Hg. This water passed 

through service deionizers, plastic hoses, and the final pflcation deionizer before going 

into the buckets. A water purity meter at the final deionizer indicated resistivity greater than 

18 MSZ-cm at all times. These observations indicate the difficulty of performing analyses at 

such low levels. The use of glass containers, properly prepared, should bepreferred over 

plastic. Some virgin plastic vessels might be suitable ifthey do not contain any inorganic 

pigments, fillers, or anti-oxidants. 

Rather than normalize results for lab-versus-field surface area-to-volume ratios, we 

performed the tests at the SAVf ratio for a 910-mm (34) diameter pipe and with soaking time 

precisely 16k1 hr. This approach was taken since concretes generally have low, but finite 

permeability. While leachate from steel pipe probably can be considered to come from the 

surface or an extremely small depth, the whole volume of a concrete specimen should be 

considered as potential source of leachable substances. Since the kinetics of heavy metal 

leaching are not precisely known and depend on individual concrete specimen permeability, 

we felt it would be useful to obtain results without "over-concentration'' of leachate followed 

by normalization, if instrument detection limits were acceptable. It will be useful to have data 

on the changing rate of leachability of trace metals as a function of conditioning time. Due to 

the apparent contamination by lead and mercury in at least some samples, it would be prudent 

to repeat the analyses for these metals. Othenvise, it appears that metals, fluoride, and nitrate 

concentrations for the two aggregates and four cements tested do not present concems in 

drinking water leachates from concrete. 

8 
ACKNOWLEDGEMENTS 

This investigation was sponsored by the Portland Cement Association under Research 

Projects 90-7 and 90-7a. Financial support from PCA is gratefully acknowledged. The 

opinions and findings expressed in this report (PCA R & D Serial No. 1925) are those of the 

authors and not necessarily those of the Portland Cement Association. The authors also wish 

to acknowledge CTL staff who contributed to this work including Willy Dziedzic (concrete 

mix designs and supervision of batching), JoAnne Delles (analytical laboratory supervisor), 

and Sebastian Padiyara (primary analyst). 

9 
Table 1. CEMENTS USED FOR CONCRETE LEACHING STUDY 

Cement No.: No. 27 No. 61 No. 82 No. 8

Cement Type: e I Type I Type IA Type 

Process Type: Preheater and Wet 

with bypass 

precalciner 

Raw Materials: 

Iron Oxide 

Sand 

Clay 

Limestone 

Fuels: 

Petroleum Coke 

Coal 

Preheater 

Shale 

Limestone Limestone 

Mill 

Sand 

CI ay 

Scale 

Iron Dust 

Natural Gas 

Iron 

Silic

Clay 

Lime

Coal PetroCoke 

Whole 

Hazardous Waste Waste Solvnts 

Tires 
Table 2. ASTM CEMENT AND MORTAR TESTS 

Blaine (ASTM C 204) 

Surface Area, cm2/g 

L.O.I. (ASTM C 114), Yo 

Insoluble Residue (ASTM C 114), % 

Mortar 3d, MPa (psi) 

Strengths (ASTM C109) 7d, MPa (psi) 

28d, MPa (psi) 

Initial Vicat (ASTM C 191), hours 

Autoclave Expansion (ASTM C 151),% 

Air Content of Mortar (ASTM C 185), % 

Cement 27 Cement 61 Cement 82 

3380 3640 4380 

0.28 

1.56 1.48 3.01 

N.D. 0.61 

22.0 (31 90) 21 .O (3050) 18.1 (2630) 

30.7 (4450) 29.6 (4300) 22.1 (3200) 

43.0 (6230) 39.8 (5770) 27.1 (3930) 

0.05 

1 :25 1 :57 2:53 

co.01 0.1 2 

9.4 8.8 18.9 

Note: N.D. value not determined. 
TABLE 3. CHEMICAL ANALYSIS OF CEMENTS, wt % 

u MAl u NQLU 

20.85 21.1 1 20.33 20.59 

4.55 4.56 4.08 

2.34 2.43 3.39 

63.88 64.05 60.47 63.69 

2.45 2.1 1 4.36 2.71 

3.34 2.85 3.00 

0.00 0.08 0.1 8 0.08 

0.51 0.62 0.79 0.52 

0.1 6 0.23 0.25 0.21 

0.02 0.1 9 0.1 0 0.06 

0.04 0.1 2 0.08 0.05 

0.04 0.03 0.07 0.1 5 

L5§ 148 u La 

99.75 99.86 100.1 1 99.62 

57 

17 

9 

7 

55 

19 

9 

7 

49 

22 

6 

10 

58 

15 

8 

9 
Analvta 

Antimony 

Arsenic 

Barium 

Beryllium 

Cadmium 

Chromium 

Lead 

Mercury 

Nickel 

Selenium 

Si Ive r 

Thallium 

Analyte 

Antimony 

Arsenic 

Barium 

Beryllium 

Cadmium 

Chromium 

Lead 

Mercury 

Nickel 

Selenium 

Si Ive r 

Thallium 

TABLE 4. TOTAL TRACE METALS IN CEMENTS, mg/kg 

<o. 19 

92.9 

1 .lo 

~0.05 

33.8 

8.1 1 

c0.062 

23 

c3 

c0.4 

46 

7.62 

<0.19 

19.0 

163 

1.65 

~0.05 

99.3 

4.62 

c0.004 

<12 

c6 

10.3 

<0.2 

co.19 

9.09 

1.32 

0.04 

65.0 

5.95 

<0.01 

21 

c4 

275 

7.06 

0.20 

<o. 1 9 

70.6 

197 

1.51 

<o. 1 3 

6.45 

0.0255 

167 

76 

<4 

~0.6 

8.03 

TABLE 5. TCLP TRACE METALS IN CEMENTS, mg/L 

No. 27 No. 61 u NQa3 

<0.0163 

co.010 

0.71 

co.ooo1 

<0.0010 

0.371 

c0.005 

c0.0006 

co. 1 9 

c0.006 

0.055 

c0.03 

c0.02 

<0.035 

0.93 

c0.0002 

0.001 07 

1.05 

0.01 a 

<0.00012 

c0.03 

<O. 005 

0.068 

~0.004 

<0.02 

<0.060 

1.58 

0.00008 

0.001 85 

0.71 3 

0.0080 

co.ooo1 

c0.05 

c0.02 

0.071 

c0.008 

0.0040 

co.019 

1.59 

0.00059 

co.oooo9 

1.22 

0.0049 

0.00023 

<0.08 

~0.004 

0.056 

-c0.007 
TABLE 6. TCLP (acid) EXTRACTS FROM AGGREGATES, mg/L 

Analvte Elain Sand Eau Claire 3/4" Eau Claire 3/8" Jhornton 

Antimony 

Arsenic 

Barium 

Beryllium 

Cadmium 

Chromium 

Lead 

Mercury 

Nickel 

Selenium 

Si Ive r 

Thallium 

c0.0022 

<0.003 

0.33 

~0.00062 

0.00068 

c0.04 

0.007 

<0.00007 

<0.08 

0.01 1 

0.0522 

0.006 

<0.0022 

~0.003 

0.33 

0.00067 

0.00046 

~0.04 

0.009 

<0.0003 

c0.08 

<0.006 

<0.01 

<0.002 

<0.0022 

~0.003 

~0.33 

0.00047 

<0.00021 

~0.04 

e0.007 

CO.08 

c0.006 

<0.01 

C0.002 

0.00008 

~0.0023 

c0.014 

0.1 6 

<0.00015 

<0.00017 

c0.07 

0.01 8 

0.00039 

0.1 8 

<0.010 

0.0422 

e0.002 
TABLE 7. CONCRETE MIX DESIGNS, kg/m3 (pcy) 

Cement 

Water 

Elgin Sand 

Coarse Aggregate 

19-1 3 mm (3/4-1/2 in) 

10-5 mm (3/&3/16 in) 

19 mm (3/4 in) topsize 

Siliceous 

Eau Claire 

335 (564) 

184 (310) 

775 (1 307) 

Calcareous 

Thornton Dolomite 

335 (564) 

184 (310) 

747 (1 259) 

695 (1 172) 

463 (781 ) 

1129 (1903) 

W/C = 0.55 

Coarse Aggregate to Sand Ratio = 60:40 
TABLE 8. PROPERTIES OF CONCRETES 

Strength 

Eau Claire Siliceous Coarse Aggregate 

@ 28 days, MPa (psi) 

Air 

Slump, mm (in.) 

Content, % 

Unit Weight, kg/m3 (pcf) 

Thornton Dolomite Coarse Aggregate 

Strength @ 28 days, MPa (psi) 

Slump, mm (in3 

Air Content, % 

Unit Weight, kg/m3 (pcf) 

44.1 (6390) 

EC-27 

1 

120 (4.7) 

.o 

33.2 (481 

TD-27 

2409 (1 50.4) 

0) 

25 (1 .O) 

1.3 

2384 (1 48.8) 

EC-6 1 

38.1 (5520) 

115 (4.5) 

t .9 

2384 (1 48.8) 

TD-61 

41.4 (601 0) 

90 (3.5) 

1.6 

2377 (1 48.4) 

Ec-82 

27.2 (3950) 

200 (7.8) 

6.2 

2291 (1 43.0) 

TD-82 

19.0 (2750) 

180 (7.2) 

6.5 

2246 (1 40.2) 
TABLE 9. TCLP (acid) EXTRACTS FROM CONCRETES, mg/L 

Analvte 

Antimony 

Arsenic 

Barium 

Beryllium 

Cadmium 

Chromium 

Lead 

Mercury 

Nickel 

Selenium 

Silver 

Thallium 

Analyte 

Antimony 

Arsenic 

Bari u m 

Beryllium 

Cadmium 

Chromium 

Lead 

Mercury 

Nickel 

Selenium 

Silver 

Thallium 

EC27 

C0.0022 

<0.008 

0.44 

<0.00004 

c0.00023 

~0.04 

<0.012 

<O. 08 

c0.006 

<0.002 

0.000346 

0.0655 

TD27 

~0.0023 

e0.005 

<O. 07 

<0.00022 

<0.00017 

0.08 

0.023 

<0.00006 

0.29 

<0.011 

0.0766 

0.007 

EC61 

~0.0025 

<0.008 

0.68 

<0.00022 

0.001 53 

0.1 9 

0.01 7 

0.000082 

co. 1 4 

<0.009 

0.1 1 

c0.002 

TD61 

~0.0023 

co.019 

0.53 

<0.00022 

<0.00017 

0.21 

0.01 9 

<0.00003 

0.1 4 

~0.005 

0.0821 

<0.002 

EC82 

c0.0025 

~0.005 

0.9 

<0.00022 

<0.00017 

0.1 9 

0.025 

0.000406 

0.17 

<0.009 

0.0766 

c0.002 

TD82 

~0.0023 

c0.007 

1.05 

<0.00022 

0.00543 

0.1 2 

0.01 6 

0.000344 

0.21 

<0.023 

0.071 

c0.002 

EC84 

0.0204 

<0.019 

0.69 

<0.00022 

c0.00017 

0.3 

0.01 3 

0.00041 6 

0.29 

e0.007 

0.0788 

0.006 

TD84 

0.01 96 

C0.013 

0.71 

<0.00022 

<0.00017 

0.22 

0.02 

0.00032 

0.3 

<0.005 

<0.01 

<0.002 
TABLE 10. TCLP (water) EXTRACTS FROM CONCRETES, mg/L 

Analvte EC82 EC84 TD82 TD84 

Antimony 

Arsenic 

Barium 

Beryllium 

Cadmium 

Chromium 

Lead 

Mercury 

Nickel 

Selenium 

Silver 

Thallium 

e0.016 

<0.0035 

0.37 

<0.0007 

<0.0013 

0.0597 

<0.022 

<0.000007 

~0.007 

<0.01 

e0.086 

<0.002 

<0.016 

<0.0035 

<0.2 

<0.0007 

<0.0013 

0.208 

<0.022 

0.000433 

<0.007 

<0.014 

~0.086 

co.001 

<0.0092 

<0.0035 

0.29 

<0.0002 

<0.0011 

c0.085 

e0.016 

0.00078 

0.0285 

e0.008 

~0.086 

<O .004 

<0.0092 

<0.022 

g0.3 

<0.0002 

<0.0011 

<o. 1 1 

<0.016 

0.000339 

0.0435 

<0.008 

<0.086 

<0.002 
Table 11. Summary of Differences 

TCLP Extracts of Concretes 

Water vs. Acetic Acid 

(concentrations in mg/L in leachate) 

Acetic Acid Water 

SAMPLE TD82 

Barium 1.05 

Cadmium 0.00543 

Chromium 0.1 2 

Nickel 0.21 

SAMPLE EC82 

Barium 0.9 

Chromium 0.1 9 

Nickel 0.1 7 

SAMPLE TD84 

Antimony 0.01 96 

Barium 0.71 

Chromium 0.22 

Nickel 0.3 

SAMPLE EC84 

Barium 

Chromium 

Nickel 

Thallium 

0.69 

0.3 

0.29 

0.006 

0.29 

<0.0011 

<0.085 

0.0285 

0.37 

0.0597 

<0.007 

~0.0092 

c0.3 

c0.11 

0.0435 

c0.2 

0.208 

c0.007 

co.001 
TABLE 12 MEASURED CONCENTRATIONS IN DRINKING WATER LEACHATES. 

aJimQkm 

control 1 

control 2 

tap water 

EC27 

TD27 

EC61 

TD61 

EC82 

TD82 

EC84 

TD84 

control 1 

control 2 

tap water 

EC27 

TD27 

EC61 

TD61 

EC82 

TD82 

EC84 

TD84 

control 1 

control 2 

tap water 

EC27 

TD27 

EC61 

TD61 

EC82 

TD82 

EC84 

TD84 

Menic (urn 

CTL TEI 

6.8 4 

6.8 <5 

4.8 da 

6.8 <5 

4.8 <5 

4.8 <5 

4.8 <5 

4.8 <5 

~2.8 <5 

42.8 <5 

42.8 <5 

Chromium (u&) 

CTL TEI 

0.2 <9 

<0.2 <9 

0.7 n/a 

0.2 <9 

<0.2 <9 

0.2 <9 

0.3 <9 

<0.2 <9 

0.2 <9 

0.3 <9 

0.3 <9 

Selenium CQ@J 

CTL TEI 

~0.3 <1 

~0.3 <1 

<0.3 n/a 

~0.3 <1 

<0.3 <1 

~0.3 <1 

~0.3 <1 

~0.3 <1 

<0.3 <1 

~0.3 <1 

~0.3 <1 

Barium 

CTL TEI 

<1 .7 60 

4.7 QO 

18 da 

4.7 QO 

g1.7 60 

4.7 QO 

2 40 

4.7 40 

4.2 40 

<1 .7 40 

4.7 QO 

Lead (ut&)* 

CTL TEI 

5.8 3 

1 .o 3 

2.7 n/a 

1.1 2 

2.1 3 

1.4 2 

0.9 2 

0.9 3 

1.2 2 

0.9 3 

1.1 4 

Silver (urn 

CTL TEI 

~0.4 <8 

<0.4 <8 

c0.4 n/a 

<0.4 <8 

<0.4 <8 

~0.4 <a 

~0.4 <8 

~0.4 e8 

<0.4 <8 

~0.4 <8 

~0.4 <8 

Cadmium (UelL) 

CTL TEI 

c0.02 

<0.02 

0.08 

c0.02 

<0.02 

<0.02 

<0.02 

c0.02 

<0.02 

g0.02 

c0.02 

4.6 

4.6 

n/a 

0.8 

4.6 

4.6 

3.7 

4.6 

~0.6 

<0.6 

<0.6 

Fluoride (m 

CTL TEI 

0.02 4.03 

0.02 <0.03 

0.5 n/a 

0.01 4.03 

0.02 <0.03 

0.01 ~0.03 

0.01 ~0.03 

0.02 ~0.03 

0.02 <0.03 

0.02 ~0.03 

0.01 ~0.03 

*Lead reporting limit 5 ppb based on 1987 Drinking Water Standard. Recently lowered lead 

?Mercury values questionable due to probable contamination. Wa" indicates not analyzed. 

standard would require reporting limit of 1.5 ppb. 
TABLE 12 CONTINUED. 

MEASURED CONCENTRATIONS IN DRINKING WATER LEACHATES. 

simwD 

control 1 

control 2 

tap water 

EC27 

TD27 

EC61 

TD61 

EC82 

TD82 

EC84 

TD84 

Nitrate-N (rng/L) 

CTL TEI 

0.06 da 

0.04 da 

0.08 da 

0.02 da 

0.03 da 

0.02 da 

0.03 n/a 

0.02 n/a 

0.04 n/a 

0.03 da 

0.02 n/a 

Notes: 

%/a" indicates not analyzed. Instrument settings and samples sizes were chosen to produce 

reporting limits generally one-twentieth or less of the Drinking Water Standards at CTL and 

one-tenth or less at TEI. That is the reason CTL minimum values are less than TEI's minimum 

values. 

For comparison, the U. S. EPA National Primary Drinking Water Standards for inorganics are 

given here in pg/L (ppb) or mgL (ppm). This list is based on the 1987 Drinking Water 

Standard found in ANSYNSF 61-1991 Appendix F which was published in May 1991. 

arsenic 50 ppb barium 1000 ppb cadmium 10 ppb chromium 50 ppb 

lead 50ppb mercury 2ppb selenium 10 ppb silver 50 PPb 

fluoride 4 ppm nitrate-N 10 ppm 

The Drinking Water Standards have been revised. A copy can be obtained from the EPA Safe 

Drinking Water Hotline at 800-426-479 1 Monday-Friday 8:30 am-5 pm EST. The inorganic 

portion of the December 1992 Standards are shown on the following two pages. 
December 1992 

. Drinking Water Standards and Heafth Advisories 

11 

Asbestos 

WOHGANICS 

lfibersn > low. 

Chlorine dioxide 

Chromium (total) 

... 

Mercury (inorganic) 

Molybdenum 

stF 

L0.006 0.006 

f . - ..... T. 

.. 

... 

0.05 

F 7 MFL 7 MFL 

F2 2 

F 0.004 0.004 

F 

L0.005 0.005 

L 

LLLLr 

- .. . .- . 

F 0.1 0.1 

F 1.3 . ' - TT" 

P 0.2 0.2 

;F 4. : '.4 . , 

F zero TT' ' :. 4 .. 0.2. ~ .;. " ..... 

:. F 0.002 0.002 '' 

.... .. 

.. 

-L; 'e. 

F 0.1 0.1 

F 10 . 10 

F1 1 t 

- 

HA' 

Ptatur 

D 

-0 - 

D 

F 

D 

f 

.D 

D 

D 

F 

:o 

. 

F 

F 

D 

O 

. .:

- 

F 

F 

F 

F 

F 

0 

-. .. .- 

0.015 0.015 

30 30 

4 0.9 

0.04 0.04 

.1 1 

1 1 

a. -. 

0.2 0.2. .. ? .._ e. 

. .. .. ...... 

0.08 

1 1 

10' 

0.01 5 

0.2 

0.2 

- 

1 

0.005 

0.9 

4 

.. 

.t 

.t . 

0.5 

0.01 

Hadth Advisorlor 

0.0 

I?. 

1 5 0.0004 

. 0.07 

0 0.005 

3 0.09 

0.02 0.0005 

1 0.1 

0.8 0.005 

0.8 

0.005 

0.14/ 

0.12 

0.022 

0.002 0.0003 

0.05 0.005 

1.7 

0.16' 

1.6 

0.02 

30 

0.6 

0.2 

0.01 

0.8 

0.2 

3.3 

0.02 

3 

0.2 

2 

0.015 

0

2

0

0

2 

0

0

0

0

0

" Copper - action level 1.3 mg.4 

Lead - action level 0.015 mg/L 
Drinking Water ,Standards and Health Advisories 

December 1992 

Beta 

RADKMlucuoEs 

panicle and photon 

activity If mmly 

man-made radionuclides) 

Radium 226R28 .. 

- .. ::. . , .. 

.. 

st- 

..;:;$: 

...... 

....... '.:!.' .: :. :.io;m ................ ., , ...... .,o.f&.':. .,: 

. i: - -. 

.. ... .. .... .- ......... 

p 

L- 

.... .. f 0.0005 0.002 

Lt- 

.......... .. t.:::: .... :+ < ;: ......... :.. ...... ... ...... ... : .......... ... ............. 

... ...* 

F zero 4 mrem 

. zero 16 pCin 

P zero 6 pCiA 

P:, zero 3M)pcJl 

P zero 20 pQR 

-I- 

... 

.. 

... 

... 

. 

- 

t 
barium 

chromium 

lead 

0.001 0.01 0.1 1 10 

Concentration, mg/L 

0 Cement27 0 Cement 61 0 Cement 82 A Cement 84 

Figure 1. Concentrations of barium, chromium, and lead in 

acetic acid TUP leachates from the four cements selected for 

this work. For comparison, the highest, lowest, and mean values 

for all cements in the PCA study of U. S. and Canadian cements 

are shown as short vertical bars. Concentrations of other 

elements are not shown since most are either below detection 

limits or far below regulatory levels. 
FIGURE 2 

.I 

.01 

,001 

e 

0 

,0001 

CONCRETE LEACHATE RELATIVE 

CONCENTRATIONS 

1/1Oth RCRA 

LEACHATE 

X 

P 

A 

0 

- 

- LIMIT 

A _1/100th 

A 

I 

e .OF LIMIT 

0 

e e 6 

A 

A 

+ r a 1 /1 OOOt h 

- OF LIMIT - 

0 t 

0 

t 

0 
FIGURE 2a 

10 

1 

.1 

.01 

CONCRETE TD84 LEACHATES 

AND ESTIMATES OF EXTREMES 

0 

0 

A 

0 

0 

e 

0 

A 

0 0 

U 

0 m 0 

0 WATER 

0 

P 
0.35 

0.3 - 

0.251 0.2 

OS1 1 

- 

0.2 0.4 0.6 0.8 1 1.2 1.4 

Chromium in TCLP cement extract, mg/L 

R=0.92 

I I I I I 

1 0 siliceous aggregate dolomite aggregate I 

Figure 3. 

0.

0.3 - 

0.25- 

0.2 - 

0.1 5- 

0.1 - 

0.05- 

a 

0 R=0.89 

of I I I I I I I 

20 40 60 80 100 120 140 160 1 

Total chromium in cement, mg/kg 

10 

0 siliceous aggregate H dolomite aggregate 

~~~ 

Figure 4. 
B 0.02 - a 

Q) 

0 

0.018- 

3 0.016- 

e 0.014- 

c 0 

0.012- H 

0 

0 

3 0.01 I I I I 

0 0.004 0.008 0.012 .016 .02 

Lead in TCLP cement extract, mg/L 

I 0 siliceous aggregate dolomite aggregate 

Figure 5. 

0.026 I 

I 0 

0.024 - 

0.022 - 

0.02 - 

0.01 8- 

0.01 6 - 

0.01 4- 

0.01 2 - 

U 

a 

0 

0 

f-. 

0.01 1 I I I I 

0 0.004 0.008 0.012 0.016 0.02 

Lead in TCLP cement extract, mg/L 

0 siliceous aggregate dolomite aggregate 

Figure 6.