Vol.11 No.05(2019), Article ID:92299,13 pages

Radiological Effects of Soil and Rock Samples of Different Libyan Regions

Abdu Assalam A. Algattawi1*, Mohammed Fayez-Hassan2, Emad Ibrahim Khalil3, Hilmy Abo Elez3

1Faculty of Technical Electronic, Tripoli, Libya

2Experimental Nuclear Physics Department, NRC, EAEA, Cairo, Egypt

3Department of Physics, Zagazig University, Zagazig, Egypt

Copyright © 2019 by author(s) and Scientific Research Publishing Inc.

This work is licensed under the Creative Commons Attribution International License (CC BY 4.0).

Received: March 17, 2019; Accepted: May 5, 2019; Published: May 8, 2019


The activity concentration of natural radioactivity for soil samples collected from western and mid Libyan regions were measured using HPGe detector. The average activity concentration of 226Ra, 232Th and 40K for ten regions was found to be 51.86 ± 7.14, 75.56 ± 10.95 and 128.98 ± 6.88 Bq/kg respectively. The results obtained for the corresponding nuclides 226Ra and 232Th are above the worldwide average values (35 and 30 Bq/kg) while 40K was smaller than worldwide average (400 Bq/kg). The average outdoor absorbed dose and the annual effective dose rates due to 226Ra, 232Th and 40K were observed to be 21.51 ± 2.93 nGy/h and 0.297 ±.03 mSv/y respectively, which are lower than world average values (60 nGy/h and 0.8 mSv/y). The radium equivalent activity and external hazard indices were found less than the world wide average values.


Activity Concentration, Absorbed Dose, Effective Dose, Activity Values, Soil Samples, Western and Mid Libya

1. Introduction

The knowledge of radionuclides distribution and radiation levels in the environment is important for assessing the effects of radiation exposure due to both terrestrial and extraterrestrial sources. Natural background radiation is of terrestrial and extraterrestrial origin. Terrestrial radiation is due to radioactive nuclides present in varying amounts in rocks, building materials, water, soils and atmosphere. Natural radionuclides of uranium 238U, thorium 232Th and potassium 40K are present in the earth’s crust. When these radionuclides and their daughters in the series undergo decays gamma rays, beta and alpha radiations are released to the environment. Therefore, human beings are continuously exposed to ionizing radiation both inside and outside their dwellings. People ingest and inhale radionuclides through their food, air and water. The gamma ray exposure in room is due to radiation emitted decay products of 226Ra, 232Th series and 40K. Human has always been exposed to natural radiation arising from the earth as well as from outside the earth [1] [2] [3] . Natural environmental radioactivity and the related external exposure due to gamma radiation depend mainly on the geological and geographical conditions, and appear at different levels in the soils of each region in the world. Every building construction material contains different quantities of natural radioactive nuclides. Radiation exposure due to building materials can be divided into external and internal exposure. The external exposure is caused by direct gamma radiation whereas internal exposure is caused by the inhalation of radon (222Rn), thorn (220Rn) and their short lived decay products. As, radon is a noble gas, it can transport easily through porous media for instance building materials, while usually only a fraction of that produced in the material reaches the surface and enters the indoor air.

The natural radioactivity in the environment is the main source of radiation exposure for human body. Natural radionuclide in soil contributes a significant amount of background radiation exposure to the population through inhalation and ingestion. It can be also transferred to plants and foods and drinking water.

According to A.L.A.R.A, principle, the radium equivalent Raeq, the external hazard index Hex the absorbed Dose Rate A.D.R and the Annual Effective Dose Equivalent. E.D.E were estimated and compared with results of other studies and with the worldwide average value. This work was undertaken to measure the activity concentrations and γ-ray absorbed doses of the naturally occurring radionuclides in soil samples. Another aim of this work is to create the public awareness about the radiation hazards and it will also be helpful to establish a research base line in the investigated regions. Some previous studies of Libyan soil, Arab and neighbors’ countries soil are summarized and tabulated in Table 1.

The two hundred samples (twenty samples for each region) were collected, at depth 1 - 10 cm. Samples were treated thermally at 60˚C for 24 hours after that they were sieved to obtain uniform particle size about 550 µm then the soil will filled in beaker which was sealed and then average weighted and stored for a month to reach the secular equilibrium.

2. Materials and Methods

Sample Collection and Preparation

The samples are selected from different geographic and geological regions in western and mid Libya. Twenty samples were collected, with average masses varied 0.24 - 0.53 kg, for each region with separate distance 1 km. The samples information is illustrated in Table 2.

Table 1. Represents the mean and range activity concentrations of radionuclides for different countries.

Table 2. Samples information.

Gamma-Ray Spectrometry

Gamma spectrometry offers a convenient, direct, and non-destructive method to measure the activity of different radionuclides in the environmental samples. It also offers high efficiency Nal(Tl) detectors and high resolution (semiconductor detectors) detection. This technique enables the use of large quantities of samples to be counted. It is also possible, in this method, to reduce the essential background to very low values using suitable shielding arrangement.

These advantages together with appropriate ability software (Genie 2000) that have now become available has made the gamma spectrometry method one of the most accurate technique for determining the activity concentration of the environmental samples. In the present work, HPGe gamma spectrometer was used for the determination of gamma active radionuclide in soil and rock samples. It is widely used for gamma ray spectroscopy to determine quantitatively the activities of natural 40K, 232Th, 226Ra in the environmental samples. The HPGe detectors have very high resolution and 70% relative efficiency. The spectrum was analyzed using multichannel analyzer (MCA) connected to computer using Genie-2000 software [15] . The sealed sample was placed in the protection unit of gamma ray spectrometry for the counting time of six hours, the energy resolution (FWHM) of this detector is 2.01 keV at 1.33 MeV (60CO).

Calibration of Gamma-ray Spectrometer System

The calibration of the spectrometer system for energy measurements is necessary to know the approximate energies of the radiation source being analyzed. The aim of calibration is to identify the radionuclide and activity concentrations present in an environmental sample. Energy calibration is carried out to confirm linear relationship between energy and the number of channels corresponding to that energy, and to determine the energy of each channel in a spectrum. The spectrum is obtained for a reasonable time so that the photo peaks have sufficient counts for analysis. The regions of interest and centroid peak channel numbers are identified.

In the present work, the detector efficiency calibration was performed using standard assurance reference materials and standard soil. These standard reference materials were taken in containers similar to the containers used for filling the soil samples for gamma spectrometric determination. The standard materials and samples were taken in containers of the same size and type so that the geometry remained the same. The samples were counted long enough (one week) to reduce the counting error.

Calculation of Activity Concentrations

The radioactivity of each sample was measured with keeping the samples one by one on the top of the detector and counted for a period of one day. The activity concentration (A) of each radionuclide in the sample was determined by using the count rates (Nc) (after subtracting the back ground).

A = N c ε I γ W (1)

where ε = Efficiency of the detector for the specific energy, Iγ = Intensity of the gamma ray and W = Sample weight (kg). For the analysis of peak areas of gamma spectra, a computer software programming (Genie 2000) was used [16] . Determination of NORM were carried out by measuring different daughters that emit clear gamma peaks of high intensity to confirm the attainment of radioactive secular equilibrium within the samples between 226Ra and its daughters. This was carried out by measuring 226Ra directly through the 186.2 keV and indirectly by measuring the 214Bi (609.3, 1120.2 and 1764.5 keV) and 214Pb (351.9 keV) photo peaks. 235U was determined directly through the 143.8 keV photo peak. 232Th was determined through 228Ac (911.2 keV), 212Pb (238.6 keV after subtract 241.2 value) and 208Tl (2614 keV) photo peaks, and estimation of 40K through the 1460.8 keV photo peak.

Computation of Radiological Effects

Radium equivalent Activity Raeq

The important radionuclides in nature 226Ra, 232Th and 40K are not uniformly distributed,this due to disequilibrium between 226Ra and its decay products.For uniformity in exposure, estimates the radionuclide concentrations have been defined in terms of radium equivalent activity (Raeq in Bq/kg). This allows comparison of the specific activity of materials (ARa, ATh and AK) containing different amounts of 226Ra, 232Th and 40K according to:

R a e q = A Ra + 1.43 A Th + 0.077 A K (2)

External and Internal Hazard Index:

The hazard index (Hex, Hin) is the indoor radiation dose rate due to the external/internal exposure gamma radiation construction materials which was calculated by:

H e x = 0.0027 A Ra + 0.0038 A Th + 2.08 × 10 4 A K (3)

H i n = 0.00541 A Ra + 0.0038 A Th + 2.08 × 10 4 A K (4)

Calculation of air absorbed dose rate:

The external outdoor absorbed gamma dose rates due to terrestrial γ-rays from the nuclides of 226Ra, 232Th and 40K at 1m above the ground level was calculated as :-

A . D . R = ( 0.461 A Ra + 0.623 A Th + 0.0414 A K ) nGyh 1 (5)

About 98% of the external γ dose rate from 238U series is delivered by the 226Ra sub series. So disequilibrium between 226Ra and 238U will not affect the results of dose calculations from the measurement of 226Ra. The absorbed dose rate was converted into annual effective dose equivalent by using conversion factor of o.7 SvGy and 0.2 for the outdoor occupancy factor by considering that the people on the average spent 20% of the time outdoors.

Effective dose rates:

The Effective dose due to natural activity in soil was calculated by:

( A . E . D . E ) in = 8760 × 0.2 × 0.7 × 10 3 A . D . R μ Svy 1 (6)

Gamma index (Iγ):

The index (Iγr) is used to estimate the level of γ ?radiation hazard associated with the natural radionuclides in specific investigated samples, is defined as:

I γ r = 0.007 A Ra + 0.01 A Th + 6.6 × 10 4 A K (7)

For materials that are used in bulk quantities the value of Iγ ≤ 0.5 corresponds to a dose rate criterion of 0.3 mSv∙yr−1 whereas 0.5 ≤ Iγ ≤ 1 corresponds to a criterion of 1 mSv∙y−1 [17]

Alpha index (Iα):

As radon daughters decay, they emit radioactive α-particles and attach to aerosols, dust and other particles in the air. As persons inhale, radon progeny are deposited on the cells lining the airways where the α-particles can damage DNA and potentially cause lung cancer. The excess α-particles radiation due to radon inhalation originating from building materials is estimated through the α-index (Iα), which is defined as follows [14] :

I α = A Ra 200 (8)

The recommended upper limit concentration of 226Ra is 200 Bq∙kg−1 which gives Iα = 1.

3. Results and Discussion

In this work the activity concentrations and radiological indices of soil samples, taken from different Libyan sites, are summarized. Activity concentrations for nuclides 235U, 226Ra, 232Th and 40K was determined by Equation (1) and the results were tabulated in Table 3 and illustrated together in Figure 1. The highest value is found for sample S10A, for 238U (226Ra) 103.81 Bq/kg, while SA4 for 232Th (153.5 Bq/kg) also SA4 for 40K (168.57 Bq/kg). The highest activity, of the nuclide, may vary from place to place due to chemical changes in elements of soil or using agriculture fertilizers or material wastes, weapons etc. The results for these nuclides are also shown independently through Figure 2.

Table 3. Average activities concentrations of the, 226Ra, 232Th and 40K in Bq/kg for the measured samples.

N.D., Not Detected.

Figure 1. The activity concentration of radionuclides for investigated samples.

Figure 2. Soil Samples of regions versus average activity concentration of radionuclides.

226Ra activity

In soil samples the activity concentrations of 226Ra were found in the range of 26 ± 0.71-103.8 ± 12.38 Bq/kg, with an average value 51.68 ± 7.14 Bq/kg.This result is higher than the world wide average value of 35 Bq/kg for the same radionuclides in soils reported by UNSCEAR.

232Th Activity

The concentration of 232Th is found in the range 40.74 ± 2.70 - 153.5 ± 7.57 Bq/kg with mean v-value 75.56 ± 10.95 Bq/kg this result is higher than the world average of 30 Bq/kg. SA1 Qarabulli). The ratio concentration of 226Ra (238U series) to 232Th is less than unity, (concentration of 232Th is higher than 226Ra) Figure 3.

40K Activity

The activity 40K is found in the range (100.35 ± 4.36) - (168.57 ± 27.26) Bq/kg with the average value of 168.98 ± 6.88 Bq/kg. This result is mostly lower than the world wide average of 400 Bq/kg but SA4 is very high for the same kind of nuclide.

To estimate the health effects, the radiation hazards such as radium equivalent (Raeq), external and internal hazard index (Hex, Hin), absorbed dose Rate (A.D.R), effective dose rate (AEDE), level index (Iγr) and α-index have been calculated from the activity of nuclides 226Ra, 232Th and 40K using the Equations (2)-(8) respectively and the values have shown in Table 4 and Figure 4.

Table 4, shows that the radium equivalent (Raeq) is found in the range (102.59 ± 20 - 292.64 ± 34.33 Bq/kg), and has average value of 157.25 ± 13.18 Bq/kg. The average value of radium equivalent is less than the safe limits 370 Bq/kg [2] . The

Table 4. Gives average activity concentration compared with others.

Figure 3. 226Ra (238U Series) to 232Th ratio.

Figure 4. Average radiological indices of the investigated regions.

mean value of external radiation hazard index is (0.45 ± 0.09) which is less than 1 and confirm it as safe to carry out the activities for the human in that region. The outdoor air absorbed dose rate due terrestrial gamma rays at 1m above the ground were calculated for 226Ra, 232Th and 40K and the range is (12.49 ± 1.66) - (34.35 ± 3.76) nGy/h with an average 21.52 ± 2.20 nGy/h which is lower than the world average of 60 nGy/h [2] . The annual effective dose rate equivalent is calculated using a conversion factor of 0.7 Sv/Gy to convert the absorbed dose rate to the effective dose equivalent and 0.2 for the outdoor occupancy factor. The annual effective dose rates are found in the range of (153.23 ± 14.50 - 263.89 ± 28.1) µSv/y with an average-e 296.75 ± 29.60 µSv/y which is lower than the world average of 1000 µSv/y for the general public (UNSCEAR, 2000). The representative level index Iγr Equation (6) must be less than unity. For the investigated samples this index is in average 1.52 ± 0.20 Bq/kg, where higher than unity in most samples.

Correlation study:

Correlation analyses were performed to reveal the possible relationship between concentrations of different radionuclides in the samples. The Pearson product-moment correlation matrixes for the correlation coefficient values (R) between the radionuclides average activity concentrations were calculated (Table 5). The correlation between 226Ra & 232Th, 226Ra & 40K and Radium and absorbed dose in air of soil samples is computed from the concentrations of these radionuclides respectively. There is a weak correlation between (226Ra, 232Th) and between (226Ra, 40K) for the samples. The value of correlation between 226Ra and absorbed dose significantly higher with positive correction [correction coefficient R = 0.99] as shown in Figure 5.

Figure 5. Correlation between 226Ra and absorbed dose.

Table 5. Average activity concentration in this work and others (Bq/kg).

4. Conclusions

The activity concentration of 226Ra, 232Th and 40K has been measured for some soil and rock samples from different locations of West and Mid Libya by using gamma-ray spectrometry (HPGe) detector. The activity of 226Ra, 232Th and 40K in samples are found to ranges from 26.71 ± 5.95 to 103.31 ± 11.28 Bq∙kg−1, 40.74 ± 4.94 to 153.5 ± 16.47 Bq∙kg−1 and 100.35 ± 9.65 to 168.57 ± 17.30 Bq∙kg−1, respectively while world average concentrations are 35, 30 and 400 Bq∙kg−1 for 226Ra, 232Th and 40K, respectively (UNSCEAR, 2000). The average and ranges of activity concentration of 226Ra, 232Th in soil of these areas are quite higher than the world average reported values (UNSCEAR, 2000) while for 40K less than world range. The average value of radium equivalent activity is 157.25 Bq∙kg−1 which is below the recommended value of 370 Bq∙kg−1. The values of absorbed dose rates due to 226Ra, 232Th and 40K in soil samples vary from 12.47 to 34.35 nGy∙h−1 with an average value of 21.52 nGy∙h−1. The calculated values of absorbed dose have been found lower than global average value. The annual effective dose rates in outdoor is found to vary from 0.153 to 0.264 mSv∙y−1 with an average value of 0.297 mSv∙y−1. This is below the limit of 1 mSv∙y−1 for general population (UNSCEAR, 2000). The calculated values of external hazard Hex are vary from 0.27 to 0.78 with an average value of 0.45 whereas internal hazard index Hin are vary from 0.34 to 1.01 with an average value of 0.59. All values of Hex and Hin are less than unity except SA10 for Hin. However, the value of gamma index Iγ is found to vary from 0.71 to 2.6 with an average value of 1.52 and most values of Iγ were also found higher than one. All the values of Alpha index Iα were found below the maximum permissible value i.e. For samples SA1, SA6, SA8 and SA10 the ratio of activity concentration (226Ra/232Th) is less than unity; this is due to that monazite contains more thorium than uranium. The obtained result in this work can be used as the regional base line data for estimation the future radioactivity contamination in the studied regions. Other studies in Libya disagree with this work due inaccuracy technique or limited regions of study [5] [6] .

Therefore, the soil of some regions used in the present study is exempted from all the restrictions concerning radioactivity, also these soil samples are safe to be used in building construction. However, the soil samples of regions as mentioned above have higher values for 232Th, 226Ra, 235U and radionuclides indices than world (UNSCEAR, 2000) [25] . The mean value of gamma index is obtained above the limit of 1 for most samples. On the basis of these results, researcher concluded that the soil of the study area (in particular regions) had radiological health hazard to the public.


I would like to thank all those people working as a team of experimental nuclear physics department NRC EAEA, who have given help and support in various ways and have made this work possible.

Conflicts of Interest

The authors declare no conflicts of interest regarding the publication of this paper.

Cite this paper

Algattawi, A.A.A., Fayez-Hassan, M., Khalil, E.I. and Elez, H.A. (2019) Radiological Effects of Soil and Rock Samples of Different Libyan Regions. Engineering, 11, 247-259.


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