Natural Radioactivity and Excess Lifetime Cancer Risk Associated with Soil in Kargi Area, Marsabit-Kenya

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1. Introduction

Radioactive elements found in rocks, soil, water, air, and in food from the earth make their way in our bodies when we breathe in air or eat foods which contain them. These naturally occurring radio isotopes such as carbon-14, potassium-40, thorium-232, uranium-238, polonium-218 and tritium (hydrogen-3) expose us to radiation from within our bodies.

Exposure to radiation is injurious to living tissues owing to its ionizing power in matter. This ionization can directly destroy living cells directly, by breaking up the chemical bonds of key biological molecules like DNA, or indirectly, by creating chemical radicles from water molecules in the cells, which can chemically attack biological molecules ( UNSCEAR, 1993 ). Somehow, these molecules are mended by use of natural biological procedures; effectiveness of this mending however depends on the size of damage. Obviously, if cell repair is not properly done or not repaired at all, the cell then may suffer either of these possible fates (Cember, 1996):

1) Cell demise

2) Cell impairment leading to somatic effects that are physical effects suffered by the irradiated person like cancer disease.

3) Genetic mutation, considered a permanent alteration of the cell and which is passed to the later generations.

The presence of radionuclides in natural environment has been noticed always. Wherever universally present in little amounts in building materials and earth, thorium together with uranium series, together with potassium 40 (^{40}K) are considered leading natural donors to external exposure from γ-radiation. (UNSCEAR, 2008).

Potassium, uranium and thorium radioactive elements together with any of their decay outcomes like radon and radium are examples of Naturally Occurring Radioactive Materials (NORM) considered long-lived. These elements have always existed in the atmosphere and earth’s crust. NORM issue relates to radon exposure in homes, particularly those built on granitic ground. By using building materials with relatively high activity concentration of ^{226}Ra and building techniques that stipulate the influx of radon from the ground e.g. well insulated housing, the radiation dose to the population dose is still further increased (Aguko et al*.*, 2013).

Approximation of the radiation dose distribution is key in gauging the health risk to a populace and serves as a reference point for registering changes in environmental radioactivity owing to anthropogenic activities (Obed et al., 2005).

Exposure to radiation for a long period of time is presumed to have some probabilities of cancer causing disease, thus everyone is at risk of contracting cancer. An additional risk that a person might have of contracting cancer disease due to long time exposure to materials causing cancer disease is called excess lifetime cancer risk (ELCR) (Qureshi et al*.*, 2014).

For outdoor occupation evaluating the terrestrial gamma dose rate, estimation of the natural radioactivity level is very important for geological samples, usually determined from the ^{40}K, ^{232}Th and ^{226}Ra contents ( UNSCEAR, 2000 ). Activity concentrations of ^{40}K, ^{232}Th and ^{226}Ra in collected soils have been estimated mainly by gamma ray spectrometry, although the fission track registration technique has also been used for the analysis of uranium concentration of these samples ( Singh et al., 2005 ). They found the absorbed dose rate as found in air, calculated the gamma dose rate from concentration of radionuclides of ^{40}K, ^{232}Th and ^{226}Ra from which they deduced the effective dose the inhabitants receive annually.

Health facilities found within and around Kargi have continuously reported a number of cancer (disease) cases together with deaths year in year out hence prompting this research work. The main aim of investigating activity concentrations together with distribution of radionuclides naturally in soil from this area was to gauge radiological health hazard together with environmental radioactivity.

2. Research Area, Sampling, Materials and Measurements

2.1. Research Area

Study Area

Kargi, found between longitudes 37˚32'34"E and 37˚36'07"E and latitudes 2˚28'37"N and 2˚31'15"N is a small village in Marsabit, Kenya covering an area of approximately 31.26 km^{2} as seen in Figure 1. Bordering Kargi is Chalbi,

Figure 1. Map showing Kargi area ( Survey of Kenya, 2017 , modified).

Gabra and Samburu.

2.2. Sampling and Materials

Sample Collection and Preparation

A total of 117 samples were collected according to the internationally established experience ( Tzortzis & Tsertos, 2004

The EPA (1995) , describes that the factors which determine the distance between sampling locations in the grid are the size of the area to be sampled and the number of samples. For each sample collection, an area of about 0.5 km x 0.5 km was marked to help get a good representation of the area. To avoid samples contamination from top soil containing leaves and other contaminations, samples were collected 10 centimetres from the surface ( Monika et al., 2010 ). These samples were packed and clearly marked before transporting to Nairobi.

Rock together with soil samples were sun dried after their collection, separately crushed in powder form to help homogenize them. Sieving the crushed

Figure 2. Sample collection plan for Kargi area ( Survey of Kenya, 2017 , modified).

powder through a 0.6 mm mesh sieve was done, oven dried for 24 hours at 100˚C to remove water completely from these samples. Crushed powder samples were individually weighed, parked in a special marked containers (plastic) before being closed tightly for about 4 weeks which was enough time to allow ^{238}U and ^{232}Th to reach secular equilibrium with their daughters before measurement of radioactivity ( Hassan et al., 2016 ).

2.3. Measurement

2.3.1. Measurement of Activity Concentration of Natural Radionuclide and Absorbed Doses

A high-purity germanium (HPGe) gamma-ray detector, 76 mm outside diameter, active volume of 144 mm^{3} with an efficiency and a resolution of 31.6% and 1.8 keV respectively was used for measurement of activity concentrations. individual sample was put in a marinelli beaker of 500 cm^{3}, filled up to same IAEA standard reference soil level (RGK-1, RGU-1 and RGTh-1) and then positioned in a lead shielded detector, adopting 22,000 - 62,000 seconds as counting time. Soil sample reference standards from International Atomic Energy Agency (IAEA) (RGU-1, RGTh-1, RGK-1 and IAEA-375 soil) were used for method validation together with calibration of spectrometer using Maestro software ( IAEA, 2003 ).

A comparative method was then employed to compute the activity concentration of each radionuclide. There were five notable gamma lines, ^{40}K line, ^{214}P_{b} and ^{214}B_{i} lines from ^{238}U and ^{212}P_{b} and ^{228}A_{c} lines from ^{232}Th for each sample. A gamma line of 1461 keV gave activity of ^{40}K, the activity of ^{238}U from 352 keV and 609 keV gamma lines of ^{214}P_{b} and ^{214}B_{i} respectively and that of ^{232}Th from 238 keV and 912 keV gamma lines of ^{212}P_{b} and ^{228}A_{c} respectively.

2.3.2. Outdoor External Gamma Dose-Rate (*D _{out}*)

The outdoor dose-rates (*D _{out}*) due to γ-radiations in air, measured 1 m above surface of ground for even spread of naturally occurring radionuclides (

${D}_{out}\left(\text{nGy}\cdot {\text{h}}^{-1}\right)=\left(0.467{C}_{Ra}+0.662{C}_{Th}+0.043{C}_{K}\right)$ (1)

where, *C _{k}*,

2.3.3. Indoor External Gamma Dose Rate (*D _{in}*)

European Commission, 1999 gives a formula for calculating indoor external dose rate as:

${D}_{in}\left(\text{nGy}\cdot {\text{h}}^{-1}\right)=\left(0.92{C}_{Ra}+1.1{C}_{Th}+0.081{C}_{K}\right)$ (2)

where, *C _{k}*,

Table 1. Sample collection plan, average activity concentration (Bq∙l^{−1}) and Radium equivalent (Bq∙l^{ −1}).

absorbed dose rates (D).

2.3.4. Radium Equivalent Activity (*Ra _{eq}*)

Radium equivalent (*Ra _{eq}*) activity, a weighted sum of

$R{a}_{eq}\left(\text{Bq}\cdot {\text{kg}}^{-1}\right)={C}_{U}+1.43{C}_{Th}+0.077{C}_{K}$ (3)

where,
${C}_{U},1.43{C}_{Th}$ and
$0.077{C}_{K}$ are activity concentrations in Bq∙kg^{−1} or Bq∙l^{−1} of ^{238}U, ^{232}Th and ^{40}K.

2.3.5. Annual Effective Dose (*De*)

Two main classification of annual effective dose are annual outdoor (*D _{out}*) and indoor (

1) Annual outdoor effective dose (*De _{out}*)

In estimating the yearly effective dose (*D _{e}*), coefficients of conversion from absorbed dose as measured in air to effective dose (0.7 Sv∙Gy

$D{e}_{out}\left(\text{mSv}\cdot {\text{y}}^{-1}\right)=D\left(\text{nGy}\cdot {\text{h}}^{-1}\right)\times 8760\text{\hspace{0.17em}}\text{h}\cdot {\text{yr}}^{-1}\times 0.4\times 0.7\text{\hspace{0.17em}}\text{Sv}\cdot {\text{Gy}}^{-1}\times {10}^{-6}$ (4)

where,

mSv∙y^{−1} (milli sieverts per year) is the unit for annual effective dose rate (*De*)

nGy∙h^{−1} (nano Gray per hour) is the unit of the absorbed dose rates (*D*)

hy∙r^{−1} (hour per year) given by 24 hours (in a day) × 365 days (in a year)

2) Annual indoor effective dose (*De _{in}*)

This can be taken as that dose a person receives while in the indoor environment and can be computed from formula 5 ( UNSCEAR, 2000 ). Annual indoor effective dose depends on time of stay inside a building, dose factors for conversion together with gamma ray dose existing within buildings.

$D{e}_{in}\left(\text{mSv}\cdot {\text{y}}^{-1}\right)=D\left(\text{nGy}\cdot {\text{h}}^{-1}\right)\times 8760\text{\hspace{0.17em}}\text{h}\cdot {\text{yr}}^{-1}\times 0.6\times 0.7\text{\hspace{0.17em}}\text{Sv}\cdot {\text{Gy}}^{-1}\times {10}^{-6}$ (5)

where,

mSv∙y^{−1} (milli sieverts per year) is the unit for annual effective dose rate (*De*)

nGy∙h^{−1} (nano Gray per hour) is the unit of the absorbed dose rates (*D*)

hy∙r^{−1} (hour per year) given by 24 hours (in a day) × 365 days (in a year)

2.3.6. Annual Gonadal Equivalent Dose (*AGED*)

UNCEAR (2000) considers bone marrow, bone surface cells and gonads to be organs of interest due to their radiation sensitivity. *AGED* increase has been known to interfere with bone marrow thereby red blood cells causing a cancer disease known as leukemia which is lethal. The *AGED* for the inhabitant using such material for building may be evaluated by the following equation (Avwiri et al*.*,2013):

$AGED\left(\mu \text{Sv}\cdot {\text{y}}^{-1}\right)C=3.09{C}_{U}+4.18{C}_{Th}+0.314{C}_{K}$ (6)

2.3.7. Excess Lifetime Cancer Risk (*ELCR*)

Potential carcinogenic effects that are characterized by estimating the probability of cancer incidence in a populace of individuals for a particular lifetime from projected exposures and intakes is called Excess Lifetime Cancer Risk (*ELCR*). Taskin et al. (2009) and Qureshi et al. (2014) calculates ELCR using Equations (7) and (8).

$ELC{R}_{in}={D}_{{e}_{in}}\times DL\times RF$ (7)

$ELC{R}_{out}={D}_{{e}_{out}}\times DL\times RF$ (8)

where,

*ELCR *= Excess Lifetime Cancer Risk

${D}_{{e}_{in}}$ = Annual indoor effective Dose

${D}_{{e}_{out}}$ = Annual outdoor effective Dose

*DL *= Average Duration of Life in year (≈70)

*RF *= Risk Factor in Sv^{−1}, that is, lethal cancer risk.

For stachostic effects, ICRP (1990) and Taskin et al. (2009) uses RF as 0.05 for public.

2.3.8. Hazard Indices

1) Hazard indices for external gamma radiation (*H _{ex}* and

Two indices were used in assessing the gamma radiation excess from materials used in building to ensure these materials safety. From the building materials, a hazard index describing the external gamma radiation dose is given as ( Beretka & Mathew, 1985

${H}_{ex}=\frac{{A}_{Ra}}{370\text{\hspace{0.17em}}\text{Bq}\cdot {\text{kg}}^{-1}}+\frac{{A}_{Th}}{259\text{\hspace{0.17em}}\text{Bq}\cdot {\text{kg}}^{-1}}+\frac{{A}_{K}}{4810\text{\hspace{0.17em}}\text{Bq}\cdot {\text{kg}}^{-1}}$ (9)

where,
${A}_{Ra},{A}_{Th}$ and
${A}_{K}$ are the activity concentrations, in Bq∙kg^{−1} of Uranium (^{238}U), Thorium (^{232}Th) and potassium (^{40}K) respectively.

For safe use of building materials, *H _{ex}* value needs to be less than unity, corresponding to 370 Bq∙kg

${I}_{\gamma}=\frac{{A}_{Ra}}{300}+\frac{{A}_{Th}}{200}+\frac{{A}_{K}}{3000}\le 1$ (10)

An exception criterion of 0.3 together with an upper limit of 1 mSv∙y^{−1} are the two dose criteria used for the gamma dose of construction materials as introduced by European Commission (EC. Many countries put in their control on 1 mSv∙y^{−1}, the upper limit. If exception criterion of 0.3 together with an upper limit of 1 mSv∙y^{−1} is taken into consideration, then *I*_{γ} values ought to be below 0.5 and 1 respectively for materials (cement and brick) used in bulk. For building materials (tiles and board) considered superficial, restricted application should be implemented and *I*_{γ}ought to be below 2 and 6 respectively, supposing values of control of 0.3 and 1 mSv∙y^{−1}.

2) Hazard indices for internal alpha radiation (*H _{in}* and

Alpha (*I*_{α}) and internal hazard (*H _{in}*) indices are the two indices used in assessing alpha radiation excess due to radon gas coming from building materials. Raghu et al. (2017) mathematically defines

${H}_{in}=\frac{{A}_{Ra}}{185\text{\hspace{0.17em}}\text{Bq}\cdot {\text{kg}}^{-1}}+\frac{{A}_{Th}}{259\text{\hspace{0.17em}}\text{Bq}\cdot {\text{kg}}^{-1}}+\frac{{A}_{K}}{4810\text{\hspace{0.17em}}\text{Bq}\cdot {\text{kg}}^{-1}}$ (11)

For safe use of materials in building construction, the computed *H _{in}* value should be less than unity.

For us to neglect the radiation hazard, values of the indices (*H _{ex}*,

Equation (12) gives the quantity* I _{α}* as:

${I}_{\alpha}=\frac{{A}_{Ra}}{200}\le 0.5$ (12)

The recommended respective values of *I*_{α} and *I*_{γ}are below 0.5 and 1 (Krieger, 1981; Raghu et al., 2017)._{ }

2.3.9. Correlation between ^{238}U and ^{232}Th, ^{238U} and ^{40}K and ^{232}Th and ^{40}K

According to Avwiri et al. (2013) , the elemental concentrations (ppm) of U-238, Th-232 together with percentage potassium can be computed from activity concentrations of Th-232, U-238 together with K-40 in Bq∙kg^{−1} as measured using the below conversion factors:

$\text{1ppmTh}=4.06\text{Bq}\cdot {\text{kg}}^{-\text{1}}$ (of Th-232) (13)

$\text{1ppmU}=12.35\text{Bq}\cdot {\text{kg}}^{-\text{1}}$ (of U-238) (14)

$\text{1}\%\text{K}=\text{313Bq}\cdot {\text{kg}}^{-\text{1}}$ (of K-40) (IAEA Technical Report No. 1363) (15)

Table 2 compares and summerises values of activities of ^{40}K, ^{232}Th, ^{226}Ra together with *Ra _{eq}* in soil samples from Kargi to those from similar investigations in other countries.

3. Results and Discussion

Calculations give specific activities of ^{238}U and ^{232}Th series as well as ^{40}K, expressed in Bq∙kg^{−1} for samples obtained from Kargi area as summerised in Table 1. Obtained values for ^{226}Ra, ^{232}Th, ^{40}K together with Ra_{eq} varied from 3.30 to 18.12

Table 2. The activities in Bq∙kg^{−1} of ^{40}K, ^{226}Ra and ^{232}Th of the samples investigated in comparison with other countries.

Figure 3. Activity values of samples due to ^{226}Ra, ^{232}Th, ^{40}K together with *Ra _{eq}* in Kargi.

Bq∙kg^{−1}, 0.00 to 17.80 Bq∙kg^{−1}, 36.87 to 667.77 Bq∙kg^{−1}, and 18.09 to 102.34 Bq∙kg^{−1} with arithmetic mean and standard deviation as 7.40 ± 2.61, 7.98 ± 4.01, 351.74 ± 109.63 and 45.90 ± 12.65 respectively. This is seen from Table 1. Globally, recommended values are respectively 37.0 Bq∙kg^{−1}, 33.0 Bq∙kg^{−1}, 400.0 Bq∙kg^{−1} ( UNSCEAR, 2008 ) and 370 Bq∙kg^{−1} ( Lu & Zhang, 2006 ). Figure 3 gives a more illustrative level of the activities.

All mean activities for ^{226}Ra, ^{232}Th, ^{40}K together with *Ra _{eq}* were less than the global values recommendation.

Mean calculated absorbed dose rates for all soil samples was 23.87 ± 3.48 nGy∙h^{−1} against the global median value of 54 nGy∙h^{−1} ( UNSCEAR, 2000 ). The values varied between 16.06 ± 1.09 and 29.35 ± 1.32 nGy∙h^{−1}, figures which are less than the required value (Table 4). The *AEDE* (*De*) values were found lower than the global value of 1 mSv∙y^{−1} ( ICRP, 2000 ) with a mean and standard deviation value of 0.14 ± 0.03 mSv∙y^{−1}, varying from 0.11 ± 0.01 to 0.18 ± 0.06 mSv∙y^{−1}.

Excess lifetime cancer risk is an added risk that one might have on contracting cancer disease if susceptible for longer time to cancer disease causing materials. Taking 70 years as mean life duration with a risk factor of 0.05 per Sv ( ICRP, 2007 ; Taskin et al., 2009 ) and a median annual effective dose rate of 0.14 mSv∙y^{−1}, then excess cancer risk is computed as 0.05%. This value is less than world agreed value of 0.145% ( Taskin et al.,* *2009

Elemental radionuclide concentrations in the samples were calculated from the activity concentrations in Bq∙kg^{−1} by use of conversion factors in Equations (13)-(15). These results are presented in Table 5. From the table, the calculated elemental concentrations ranged from 0.74% to 1.51%, 0.68 to 3.04 ppm and 0.33 to 0.97 ppm for potassium, uranium and thorium respectively with respective arithmetic mean and standard deviation of 1.13% ± 0.21%, 1.98 ± 0.47 ppm, 0.59 ± 0.13 ppm.

Tzortzis & Tsertos (2004) and Al-Hamarneh & Awadalla (2009) noted that a high or low value of Th/U ratios as measured in some studied locations may be an indication of a uranium depletion or thorium enrichment due to natural processes alteration in that area. They approximated the theoretical normal continental crust values of Th/U elemental ratios to be 3.0. From Table 5, our Th/U results ranged from 1.19 ± 0.85 to 6.35 ± 1.72 with mean and standard deviation of 3.57 ± 1.13. Other correlation ratios of K/U together with K/Th varied from 0.84 ± 0.46 to 3.89 ± 2.13 together with 0.34 ± 0.09 to 1.94 ± 2.42 with mean and standard deviations of 2.15 ± 0.67 and 0.68 ± 0.30 respectively.

Correlations existing between activities ^{232}Th and ^{238}U, ^{40}K and ^{238}U together with ^{40}K and ^{232}Th showed a weak relationship existing on ^{232}Th against ^{238}U, ^{40}K against ^{238}U together with ^{40}K against ^{232}Th with correlation coefficients of 0.405, 0.134 and 0.319 respectively.

Respective mean values together with their standard deviations of representative alpha (*I*_{α}), representative gamma *(I _{γ}*), internal hazard (

4. Conclusion

Results from the study give the mean activities for the area as 354.81 ± 67.06, 7.23 ± 1.67 and 8.03 ± 1.91 Bq∙kg^{−1} against the world standard values of 400, 35 and 30 Bq∙kg^{−1} for ^{40}K, ^{226}Ra together with ^{232}Th ( UNSCEAR, 2000 ) respectively. The area generally cannot be classified as a High Background Radiation Area (HBRA), thus good for human settlement.

Mean evaluated absorbed dose rate was below recommended values by almost half. Annual effective dose rate values were found lower than global value of 1

Table 3. Calculated values of representative alpha (*I*_{α}), representative gamma (*I _{γ}*), internal hazard (

Table 4. Gamma dose rates, *AEDE* (*De*) and excess lifetime cancer risk (*ELCR*) as per sources.

Table 5. Elemental concentration of specific activity of ^{40}K, ^{238}U together with ^{232}Th (ppm) in samples with their ratios.

Figure 4. Hazard indices values for entire Kargi area.

mSv∙y^{−1}, which, for the public exposure is the annual effective dose rate limit ( ICRP, 2000 ).

Hazard indices (*H _{in}*,

Excess cancer risk, calculated from the samples showed lower values hence minimal chance of getting cancer disease. The area is safe from cancer causing radionuclides.

Because Th/U value was higher than the recommended, the study can therefore conclude that there could have been a fractionation during weathering or involvement of metasomatic activity of the radioelements.

Acknowledgements

The authors thank Jomo Kenyatta University of Agriculture & Technology (JKUAT), Kenya Bureau of Standards (KEBS) for their mass measurements and oven drying facility, University of Nairobi’s Nuclear Science and Technology Institute (INST) for laboratory analysis and γ-ray spectrometer, Kargi administration, my family and Research assistant, Lydia Okemwa of Technical University of Kenya, TUK.

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