Ingestion of radioactively contaminated diets for two generations in the pale grass blue butterfly
© Nohara et al.; licensee BioMed Central Ltd. 2014
Received: 23 May 2014
Accepted: 19 August 2014
Published: 23 September 2014
The release of radioactive materials due to the Fukushima nuclear accident has raised concern regarding the biological impacts of ingesting radioactively contaminated diets on organisms. We previously performed an internal exposure experiment in which contaminated leaves collected from polluted areas were fed to larvae of the pale grass blue butterfly, Zizeeria maha, from Okinawa, which is one of the least polluted localities in Japan. Using the same experimental system, in the present study, we further examined the effects of low-level-contaminated diets on this butterfly. Leaves were collected from two localities in Tohoku (Motomiya (161 Bq/kg) and Koriyama (117 Bq/kg)); two in Kanto (Kashiwa (47.6 Bq/kg) and Musashino (6.4 Bq/kg)); one in Tokai (Atami (2.5 Bq/kg)); and from Okinawa (0.2 Bq/kg). In addition to the effects on the first generation, we examined the possible transgenerational effects of the diets on the next generation.
In the first generation, the Tohoku groups showed higher rates of mortality and abnormalities and a smaller forewing size than the Okinawa group. The mortality rates were largely dependent on the ingested dose of caesium. The survival rates of the Kanto-Tokai groups were greater than 80%, but the rates in the Tohoku groups were much lower. In the next generation, the survival rates in the Tohoku groups were below 20%, whereas those of the Okinawa groups were above 70%. The survival rates in the second generation were independent of the locality of the leaves ingested by the first generation, indicating that the diet in the second generation was the determinant of their survival. Moreover, a smaller forewing size was observed in the Tohoku groups in the second generation. However, the forewing size was inversely correlated with the cumulative caesium dose ingested throughout the first and second generations, indicating that the diet in the first generation also influenced the forewing size of the second generation.
Biological effects are detectable under a low ingested dose of radioactivity from a contaminated diet. The effects are transgenerational but can be overcome by ingesting a non-contaminated diet, suggesting that at least some of the observed effects are attributable to non-genetic physiological changes.
The collapse of the Fukushima Dai-ichi Nuclear Power Plant (NPP) due to the Great East Japan Earthquake on 11 March 2011 resulted in the release of a massive amount of radioactive materials into the surrounding environment. This large-scale environmental pollution has impacted the lives of organisms living in the polluted areas. A field study revealed that the number of butterflies decreased in the polluted areas ,, and morphological abnormalities have been detected in aphids from Fukushima . However, such studies examining the biological impacts of the accident are still scarce.
Our group has been studying the development and evolution of butterflies in response to environmental stress . One of our favourite butterflies is a small lycaenid butterfly, the pale grass blue, Zizeeria maha (Lepidoptera, Lycaenidae), which is found throughout Japan, except in Hokkaido -. Using this butterfly as an experimental system, we previously reported various morphological abnormalities and a smaller forewing size in adults collected from highly polluted areas -. We showed that some abnormal traits, including aberrations in the wing colour pattern, were heritable, suggesting genetic damage introduced by the accident -. We believe that the proposed genetic damage was introduced mainly by the initial exposure of the butterflies immediately after the explosion . We reproduced these field-based results through an external exposure experiment in which butterfly larvae and pupae were raised near an artificial caesium radiation source as well as through an internal exposure experiment in which larvae consumed contaminated host plant leaves collected from polluted areas -. High mortality and abnormality rates were detected , and a small forewing size (i.e., body size) was also observed , similar to the outcome of the food stress in butterflies .
Information for the collection localities for host plant leaves
Distance from the NPP [km] (average)
Ground radiation [μSv/h] (average)
1 Senbaru, Nishihara, Okinawa Prefecture, University of the Ryukyus
20, 30 July 2012
0.05 (8 April 2012)
2-22 October 2012
1164 Izusan, Atami City, Shizuoka Prefecture
25 July 2012
4 August 2012
2 Gotenyama, Musashino City, Tokyo
24 July 2012
3 August 2012
20 October 2012*1
6 Kashiwanoha, Kashiwa City, Chiba Prefecture
23 July 2012
7 August 2012
5 October 2012*1
Tomita, Koriyama City, Fukushima Prefecture
4, 14 October 2012
1 November 2012
Arai, Motomiya City, Fukushima Prefecture
4, 14 October 2012
1 November 2012
Effects on the F1 generation
Caesium radioactivity in host plant leaves* 1
Activity of137Cs (±SE) [Bq/kg]
Activity of134Cs (±SE) [Bq/kg]
Total for137Cs and134Cs [Bq/kg]
Okinawa (for F1)
0.12 ± 0.02
0.06 ± 0.02
0.18 ± 0.03
Atami (for F1)
1.48 ± 0.06
1.05 ± 0.06
2.53 ± 0.08
Musashino (for F1)
3.82 ± 0.07
2.56 ± 0.07
6.38 ± 0.10
Kashiwa (for F1)
28.40 ± 0.33
19.17 ± 0.32
47.57 ± 0.46
Koriyama (for F1)
71.87 ± 0.40
45.34 ± 0.37
117.21 ± 0.54
Motomiya (for F1)
98.19 ± 0.54
62.41 ± 0.49
160.60 ± 0.73
Okinawa (for F2)
0.11 ± 0.02
0.06 ± 0.02
0.18 ± 0.03
Koriyama (for F2)
71.73 ± 0.40
44.07 ± 0.36
115.80 ± 0.54
Motomiya (for F2)
98.00 ± 0.53
60.65 ± 0.48
158.65 ± 0.72
Ingested caesium dose and mortality and abnormality rates in the F 1 generation
The F1leaves from:
Number of larvae (n)
Ingested caesium dose [mBq]
Mortality rate [%]
Total abnormality rate [%]
308 (Summer = 67, Fall = 241)
0.0629 ± 0.0011
0.883 ± 0.003
2.23 ± 0.004
16.6 ± 0.02
40.9 ± 0.02
56.1 ± 0.03
Because surviving adults are not necessarily healthy regarding morphological traits, we calculated relative normality values for adults in reference to the control Okinawa groups as an indication of the robustness of each feeding group (Figure 2b). To this end, the ratio of the number of morphologically normal (non-abnormal) adults to the original number of larvae was calculated, and the ratios in the control Okinawa groups were set at 100%. As expected, the robustness distribution (y) appeared to show a non-significant inverse response relationship with the caesium dose (x) with the regression model, y = −0.53 (±0.24) x + 89.07 (±6.23) (R2 = 0.555, df = 5, F = 4.99, p = 0.089). When the Motomiya sample was excluded as an outlier, the regression equation becomes y = −1.03 (±0.17) x + 92.37 (±3.41) (R2 = 0.923, df = 4, F = 35.95, p = 0.0093), showing a highly significant dose–response relationship and being consistent with the results found for the mortality rates.
We noted that the Motomiya and Koriyama curves showed a great deal of mortality in the larva-prepupa period. The curves were segregated into three clusters of groups: a high survival cluster (Okinawa, Ube, Atami, Musashino, and Kashiwa), an intermediate survival cluster (Hirono and Motomiya), and a low survival cluster (Iitate-montane, Koriyama, Fukushima, and Iitate-flatland). These three clusters were statistically different from one another (df = 3, χ2 = 286, p < 0.0001, log rank test; df = 3, χ2 = 276, p < 0.0001, Wilcoxon rank test). However, the concentrations of caesium activity recorded in the leaves showed great variation within a given cluster. This intra-cluster variation most likely occurred because these groups were implemented using three different genetic lines of this butterfly species in different time periods, suggesting intraspecific variation regarding sensitivity to a radioactively contaminated diet. Accordingly, a set of groups that were assessed within the same time period were found to be comparable to one another as they come from the same genetic line (see Methods).
Effects on the F2 generation
Ingested caesium dose in the F 2 generation
Number of larvae (n)
Ingested caesium dose [mBq]
522 (=170 + 128 + 224)
0.0629 ± 0.0011
290 (=158 + 132)
40.4 ± 0.02
516 (=158 + 358)
55.4 ± 0.03
Mortality and abnormality rates in the F 2 generation* 1
MR = 16.5%;
MR = 79.1%;
MR = 89.9%;
AR = 18.8%
AR = 79.7%
AR = 90.5%
(n = 170)
(n = 158)
(n = 158)
MR = 10.2%;
MR = 78.8%;
AR = 15.6%
AR = 87.9%
(n = 128)
(n = 132)
MR = 22.8%;
MR = 99.2%;
AR = 29.9%
AR = 99.2%
(n = 224)
(n = 358)
Pearson correlation coefficient r and p -values for the F 2 generation between the ingested caesium dose and forewing size
Male, F2 only
Male, F1 + F2
Female, F2 only
Female, F1 + F2
In the present study, we performed an internal exposure experiment using contaminated host plant leaves. The host plant leaves were collected from the localities showing low-level contamination, including two localities in Tohoku (Koriyama and Motomiya), two in Kanto (Kashiwa and Musashino), and one in Tokai (Atami). A similar experiment was performed previously , and the present study therefore serves to reproduce and validate the previous results. Furthermore, the present study extends the previous study by using the leaves that were less contaminated than those used in the previous study.
In the present study, low-dose effects were clearly detected in the butterflies in the form of high mortality and abnormality rates, low normality rates (robustness), low survival rates, and a small forewing size in the F1 generation of the Tohoku groups. It was somewhat surprising to find that the Koriyama group, which ingested 40.9 mBq of radioactive caesium during the larval stage from contaminated-contaminated leaves showing an activity of 117 Bq/kg, displayed mortality and abnormality rates greater than 50%, although the Motomiya group exhibited somewhat lower rates. These results suggest that low-dose ingestion of approximately 100 Bq/kg may be seriously toxic to certain organisms. Even among the surviving adults, a small forewing size was detected in the Koriyama and Motomiya groups, confirming the results concerning mortality rates, abnormality rates, normality rates, and survival rates.
For the Kanto and Tokai localities, which presented relatively low contamination levels ranging from 2.53 Bq/kg to 47.57 Bq/kg, both the mortality (survival) rates and the abnormality (normality) rates appeared to be dose dependent. These Kanto-Tokai groups were tested using the same genetic lines at the same time, which were comparable to one another. Therefore, the contaminated leaves from the Kanto-Tokai districts may have had small but detectable effects on the fitness of the butterflies. On the other hand, the forewing size of males in the Kanto-Tokai groups appeared to be larger than that of the Okinawa group, despite the possible adverse effects detected for other measures (Figure 3). The reasons for this size increase are not clear. The biological responses to very low doses may simply be different from the responses to relatively high doses.
Interestingly, the survival curves obtained for the different localities were segregated into three clusters: high, intermediate, and low survival clusters, not only among the groups from the previous study , but also in the groups of the present study, despite the large difference in caesium activity levels between the previous and present studies. In the previous study , the half mortality rate was calculated as 1.9 Bq per larva, corresponding to constant leaf consumption of 4.9 × 103 Bq/kg throughout the larval stage. These previous values were more than 40 times as high as the values we obtained for Koriyama in the present study. As a result, within a given cluster of survival curves, the levels of leaf contamination were highly variable (see Figure 4). However, within a given set of groups that were treated within the same time period (hence, coming from the same genetic line), the survival rates were largely dependent on the caesium activity in the leaves. These results may originate simply from a dependence of radiation sensitivity on the genetic background of butterfly lines. That is, direct comparison between different butterfly lines may be difficult, even if the experimental set-ups are virtually identical with the exception of their genetic makeup. Therefore, our results suggest the existence of intraspecific individual variation of sensitivity to low-level radiation, which is consistent with the existing literature .
The biological effects of ingesting the contaminated diets were more severe in the F2 generation, despite the normal morphological appearance of their F1 parents. The differences can be illustrated as follows: The mortality rates of the Koriyama F1 group and the Koriyama F2 group obtained from the Koriyama F1 adults were 53.0% and 79%, respectively, while the mortality rates of the Motomiya F1 group and the Motomiya F2 group obtained from the Motomiya F1 adults were 31.2% and 99%, respectively. As the mortality rates of the Okinawa F1 group and the Okinawa F2 group obtained from the Okinawa F1 adults were 8% and 17%, respectively, the increase in mortality rates observed in the F2 generation cannot be readily attributed to the transgenerational accumulation of radiation effects. However, effects of the F1 generation on the F2 generation were discernable in the form of a small forewing size and its high correlation with the cumulative caesium dose, especially in females. It is important to note that a small forewing size can be induced not only through feeding of contaminated leaves, but also through long-term low-dose external irradiation in this species . Furthermore, a small forewing size has been detected in field-caught butterflies from the polluted areas . Therefore, the small forewing size observed in the present study implies that internal radiation exposure may have contributed to the high mortality rates recorded. Nevertheless, the F1 effect was small, and it could largely be overcome by the consumption of Okinawa leaves or amplified by the consumption of Koriyama or Motomiya leaves in the F2 generation. That is, the effects were transgenerational, but largely non-genetic physiological effects that could be overcome by dietary changes. Mechanistically, these outcomes may be explained by maternal effects, epigenetic effects, genomic instability, or similar phenomena.
These results potentially conflict with our previous findings showing that morphological abnormalities, including wing colour pattern aberrations, found in the F1 generation were heritable by the F2 generation -. In this previous experiment, we used P-generation adults collected from the field in the spring of 2011. These P-generation individuals were directly exposed to all of the radioactive materials from the explosion of the NPP when they were larvae, which could have resulted in genetic damage. We then employed morphologically abnormal F1 adults to obtain the F2 generation using non-contaminated leaves. In the case of the possible genetic damage indicated in 2011, the larvae may have consumed radioactive materials adsorbed on the surface of leaves. The contributions of β-ray-emitting nuclides in the earlier experiment cannot be ignored . In contrast, the present study was performed in 2012, when the major radioactive species present was caesium, and the surface adsorption of radioactive materials was likely much less extreme. Therefore, the probability of genetic damage resulting from the ingestion of a contaminated diet was rather low in the present study. Both experimental set-ups are reasonable for examining heritable effects that are likely based on either genetic or physiological (or epigenetic) changes.
In the examination of forewing size, we noted a sex difference. Females showed a higher correlation with the ingested dose of radioactivity in both the F1 and F2 generations than males. The reasons for this sex difference are not clear. However, higher sensitivity of females to cold shock, a type of environmental stress, has been reported in this species of butterfly . Hence, it is likely that females are generally more sensitive to stress than males of this species.
The internal exposure of organisms living in a polluted area through a contaminated diet is unavoidable. Indeed, the possible biological effects of contaminated diets on humans after the Chernobyl accident have been documented ,. However, to the best of our knowledge, controlled experimental evaluations of internal exposure via a consumed diet are scarce in any organism in the field of radiation biology, with a few possible exceptions , although there may be some anecdotal or non-published studies that were performed following the Chernobyl accident. Thus, our experimental results constitute an important contribution to the research field. Accumulation of such scientific evidence is required to establish the low-dose biological effects of radiation .
Our experimental system for detecting the biological effects of internal exposure to radiation via contaminated diets revealed that low-dose ingestion likely causes death (i.e., high mortality and low survival rates), disease (i.e., high abnormality and low normality rates), and growth retardation (i.e., a small forewing size), at least in some individuals of the pale grass blue butterfly. The effects of ingesting a contaminated diet on survival rates and forewing size were shown to be transgenerational. However, the effects of ingesting a contaminated diet in the F1 generation could be largely overcome by ingesting a non-contaminated diet in the F2 generation. It is likely that at least some of the biological effects of internal exposure to low doses of radiation are attributed to non-genetic physiological (or epigenetic) changes.
No specific permissions were required to collect the pale grass blue butterfly Z. maha and its host plant of O. corniculata in Japan. The pale grass blue butterfly is the most common butterfly in Japan, and its host plant is a weed that is often a target for eradication in gardening and agriculture.
We followed standard rearing methods we have described previously , with a few minor modifications ,. The egg collection procedure was also described elsewhere . A pool of females was caught in the field in Okinawa (defined as the P generation) and used to collect eggs (defined as the F1 generation or the first offspring generation). These eggs were divided into four (in the summer of 2012) or three (in the fall of 2012) feeding groups in the F1 generation. Therefore, the genetic differences among these feeding groups could be ignored. Eggs were similarly obtained from a different pool of females caught in the field in Okinawa and were then divided into three feeding groups. These groups were fed leaves from Okinawa, Koriyama, or Motomiya. These additional three groups were employed in crosses with the first-generation groups to obtain the next generation (defined as the F2 generation or the second offspring generation). This process was necessary to avoid sibling crosses that could adversely affect the robustness of the offspring. To obtain the F2 eggs, morphologically normal and healthy (non-abnormal) adults were selected from one F1 group and mated with healthy adults from a different F1 group. In this paper, a group that consumed leaves from locality A in the F1 generation and leaves from locality B in the F2 generation is often indicated as the A-B group, but these butterflies all came from Okinawa lines genetically. All rearing experiments were performed in our laboratory, located on the Nishihara Campus of the University of the Ryukyus, Okinawa, except for the rearing of the Kanto-Tokai groups, which was carried out in our branch at Kichijouji, Musashino City, Tokyo, where the radiation level was maintained at 0.04-0.05 μSv/h, with the windows being closed at all times.
Collection of host plant samples
Bunches of the host plant leaves of O. corniculata were collected from various localities in the summer and fall of 2012, as shown in Table 1. The bunches were covered with wet paper, stored in a chilled container, and sent to the laboratory, where they were stored in a refrigerator until use. The leaves stored in this way were still fresh when they were given to larvae. The bunches were stored separately, depending on the collection locality, to prevent cross contamination. Feeding experiments using the leaves from the Kanto and Tokai localities (Kashiwa, Musashino, and Atami) and Okinawa were performed in the summer of 2012, and feeding experiments using the leaves from the Tohoku localities (Koriyama and Motomiya) and Okinawa were performed in the fall of 2012.
Forewing size measurement
We used an SKM-2000 digital microscope and the associated software SK Measure (Saito Kougaku, Yokohama, Japan) to measure forewing size in digital images. We measured the distance from the base to the marginal band at the end of the M1 vein on the ventral side. Because the feeding experiments involving leaves from the Kanto and Tohoku localities were performed separately, the Okinawa groups for the summer and fall experiments were both set at 1.00 in Figure 3, so that their results could be shown in a single graph.
Measurement and calculation of radioactivity
The ground radiation dose at the collection sites was measured using an Aloka TCS-161 scintillation survey meter (Hitachi Aloka Medical, Tokyo, Japan) or an RAE Systems DoseRAE 2 dosimeter (San Jose, CA, USA) on the surface of the ground (0 cm high). Radioactivity measurements of caesium in the host plant and pupal samples were performed using a Canberra GCW-4023 germanium radiation detector (Meriden, CT, USA) at the Instrumental Research Center of the University of the Ryukyus. Measurements were also performed using an Ortec GMX30 N-type HP germanium detector (Oak Ridge, TN, USA) at Nagasaki University to check the reproducibility of the measurements. The host plant samples were dried and burned to ashes (flameless combustion) before being subjected to measurements, as described previously ,. Pupal samples were measured in a small columnar plastic container as indicated in a previous report , but the results were all below the detection limit.
To calculate the amount of caesium ingested, we assumed that the larvae hatched on the sixth day following egg deposition, and they were subsequently fed Okinawa leaves for eight days, after which contaminated leaves from the different localities were provided. Thus, for the first 14 days after egg deposition, all larvae consumed Okinawa leaves. Based on previous data , we estimated that approximately 10% of the entire amount of leaves that a larva consumed came from Okinawa leaves, which was taken into account to calculate the ingested caesium dose. Furthermore, for simplicity, we assumed that the larvae ate all of the leaves required for subsequent growth at once on the first day of ingestion of the contaminated leaves and that 137Cs and 134Cs were released at a 1:1 activity ratio on 15 March 2011 in a single burst from the Fukushima Dai-ichi NPP.
Statistical analysis and graphics
We used the statistical software R version 3.0.2 (R Foundation for Statistical Computing, Vienna, Austria), JSTAT version 13.0 (Yokohama, Japan), and JMP 11.0.0 (2013) (SAS Institute, Cary, NC, USA). Linear regression equations were expressed with standard error and accessed with R2 and p-values. Data were also evaluated with Pearson correlation coefficient r. To assess forewing size differences, either Student’s or Welch’s t-test was performed, in accordance with F-test. Survival curves were examined by log rank test and Wilcoxon rank test. Data were graphically presented using Excel (2013) (Microsoft).
We thank J. Nohara (Tokyo), M. Hatta (Ube), J. Ishida (Okuma), N. Itou (Iitate), K. Yoshida (Minami-soma), K. Nakanome (Minami-soma), and K. Morizono (Koriyama) for their help in collecting host plant leaves and K. Yoshida (Minami-soma) for technical assistance. We also thank M. Iwasaki and other members of the BCPH Unit of Molecular Physiology for discussion and technical help. This work was supported in part by the Grant for Environmental Research Projects from The Sumitomo Foundation, Tokyo, Japan, and by the Incentive Project of the University of the Ryukyus.
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