# Strategies and effectiveness of land decontamination in the region affected by radioactive fallout from the Fukushima nuclear accident: A review

O. Evrard, J. Patrick Laceby, Atsushi Nakao

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O. Evrard, J. Patrick Laceby, Atsushi Nakao. Strategies and effectiveness of land decontamination in the region affected by radioactive fallout from the Fukushima nuclear accident: A review: SOIL Discussions. 2019. cea-02812441

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1 Strategies and effectiveness of land decontamination in the region affected by radioactive fallout

2 from the Fukushima nuclear accident: A review

3 Olivier Evrard¹, J. Patrick Laceby², Atsushi Nakao³

4 ¹Laboratoire des Sciences du Climat et de l'Environnement (LSCE/IPSL), Unité Mixte de Recherche 8212 (CEA/

5 CNRS/UVSQ), Université Paris-Saclay, Gif-sur-Yvette, France.

6 ²Environmental Monitoring and Science Division (EMSD), Alberta Environment and Parks (AEP), Calgary, Alberta,

7 Canada.

8 ³Graduate School of Life and Environmental Sciences, Kyoto Prefectural University, Kyoto, Japan.

9

10 Correspondence to: Olivier Evrard (olivier.evrard@lsce.ipsl.fr).

11 Abstract

12 The Fukushima Dai-ichi Nuclear Power Plant (FDNPP) accident in March 2011 resulted in the
13 contamination of Japanese landscapes with radioactive fallout. Accordingly, the Japanese authorities
14 decided to conduct extensive remediation activities in the impacted region to allow for the relatively
15 rapid return of the local population. The objective of this review is to provide an overview of the
16 decontamination strategies and their potential effectiveness in Japan, focussing on particle-bound
17 radiocesium. In the Fukushima Prefecture, the decision was taken to decontaminate the fallout-
18 impacted landscapes in November 2011 for the 11 municipalities evacuated after the accident (Special
19 Decontamination Zones – SDZ, 1117 km²) and for the 40 non-evacuated municipalities affected by
20 lower, although still significant, levels of radioactivity (Intensive Contamination Survey Areas, 7836
21 km²). Decontamination activities predominantly targeted agricultural landscapes and residential areas.
22 No decontamination activities are currently planned for the majority of forested areas, which cover
23 ~75% of the main fallout-impacted region. Research investigating the effectiveness of
decontamination activities underlined the need to undertake concerted actions at the catchment scale
24 to avoid the renewed supply of contamination from the catchment headwaters after the completion
25 of remediation activities. Although the impact of decontamination on the radioactive dose rates for
26 the local population remains a subject of debate in the literature and in the local communities, outdoor
27 workers in the SDZ represent a group of the local population that may exceed the long-term dosimetric
28 target of 1mSv yr⁻¹. Decontamination activities generated ~20 million m³ of soil waste by early 2019.
29 The volume of waste generated by decontamination may be decreased through incineration of
30 combustible material and recycling of the less contaminated soil for civil engineering structures.
31 However, most of this material will have to be stored for ~30 years at interim facilities opened in 2017
32 in the close vicinity of the FDNPP before being potentially transported to final disposal sites outside of
33 the Fukushima Prefecture. Further research is required to investigate the perennial contribution of
34 radiocesium from forest sources. In addition, the re-cultivation of farmland after decontamination
35 raises additional questions associated with the fertility of remediated soils and the potential transfer
36 of residual radiocesium to the plants. Overall, we believe it is important to synthesize the remediation
37 lessons learnt following the FDNPP nuclear accident, which could be fundamental if a similar
38 catastrophe occurs somewhere on Earth in the future.
39

40

41 **Keywords:** radiocesium; caesium-137; FDNPP; remediation; nuclear accident; Japan.

42
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43 **1. Introduction**

44 Large quantities of radiocesium (12–62 PBq) were released into the environment by the Fukushima
45 Dai-ichi Nuclear Power Plant (FDNPP) accident in March 2011 (Stohl et al., 2012; Chino et al., 2011).
46 Airborne and ground contamination surveys demonstrated that the contamination was the highest
47 (i.e., initial ¹³⁷Cs levels >100,000 Bq m⁻²) in a plume extending to the northwest of the FDNPP covering
48 an area of ~3000 km² (Kinoshita et al., 2011; Chartin et al., 2013; Yasunari et al., 2011). Although many
49 radioactive substances were released into the environment by the FDNPP accident, radiocesium (i.e.,
50 ¹³⁴Cs and ¹³⁷Cs) presents the most serious risk to the local population over the medium to long term as
51 it was emitted in very large quantities and it has a relatively long half-life (i.e., ¹³⁴Cs - 2 years; ¹³⁷Cs - 30
52 years) (Steinhauser et al., 2014).

53 Numerous investigations have been conducted by Japanese and international researchers to improve
54 our understanding of the fate of radiocesium in the Fukushima region (for a review, see: Evrard et al.,
55 2015). In general, radiocesium sorption mechanisms were characterised (Fan et al., 2014; Nakao et al.,
56 2015) and their fluxes measured in riverine systems draining the main radioactive plume (Nagao et al.,
57 2013). Land use (Koarashi et al., 2012) and soil properties (Nakao et al., 2014) were shown to control
58 the migration of radiocesium in soils. Accordingly, the fate of this contaminant was intensively
59 investigated in forest ecosystems (Gonze and Calmon, 2017) and cultivated landscapes (Yoshimura et
60 al., 2016), which are the two main land uses in the fallout-impacted region. Typhoons and other major
61 rainfall events were also demonstrated to drive soil erosion and sediment migration processes thus
62 directly influencing post-fallout radiocesium dynamics (Chartin et al., 2017).

63 Between 2011–2018, there were 578 published studies with the keywords ‘radiocesium’ and
64 ‘Fukushima’ in the Scopus database (Figure 1). Approximately 90% of these articles were published by
65 Japanese scientists, demonstrating the extensive research effort conducted by the national scientific
66 community in Japan on the processes occurring in this post-accidental context. Since the second half
67 of 2013, remediation activities started to be implemented under the supervision of the Japanese
68 authorities to decontaminate soils. These activities have significantly affected the spatial and temporal
69 redistribution of radionuclides in the Fukushima-impacted area. As decontamination is now completed
70 in many regions and more than 50 scientific studies have been conducted on different aspects of these
71 operations (Figure 1), synthesizing the results obtained by this applied research is important for the
72 scientific community. Of note, this review will not synthesize non-peer reviewed reports published by
73 the Japanese authorities, although numerous resources are available on the official websites of
74 multiple Japanese ministries (Table 1).

75 Although radiocesium is mainly transported in particle-bound form in the Fukushima fallout-impact
76 area (Konoplev et al., 2016), dissolved radiocesium was found in numerous environmental
77 compartments, primarily during the immediate post-accidental phase (Yoshimura et al., 2014). As most
78 of the dissolved radiocesium migrated through these landscapes immediately after the FDNPP
79 accident, this literature review will focus on particulate radiocesium. Furthermore, as ¹³⁴Cs and ¹³⁷Cs
80 were emitted in equivalent proportions into the environment in March 2011, with an initial ¹³⁴Cs/¹³⁷Cs
81 activity ratio of ~1 (Kobayashi et al., 2017), this review will focus primarily on ¹³⁷Cs owing to its longer
82 half-life and thus greater risk to the local population over the medium to long-term. Accordingly, the
83 goal of this review is to examine the remediation strategies and their effectiveness for particulate
84 bound ¹³⁷Cs in Japan.

85 This literature review will be divided into five main sections. First, the spatial extent of the
86 decontaminated zone and the schedule of these remediation activities will be outlined. Second, the
87 remediation strategies in different environments (i.e., farmland, river, forests) will be presented along
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88 with a summary of their cost effectiveness. Third, the impacts of remediation activities on dosimetry
89 will be summarized. Fourth, the initiatives to manage the large volume of waste generated by
90 remediation will be discussed. Fifth, major research questions and requirements to guide the future
91 management of Fukushima fallout-impacted areas will be identified and presented. The objective of
92 this review is to provide a synthesis of the remediation lessons learnt in Japan following the FDNPP
93 nuclear accident, which are fundamental in light of the potential for a similar catastrophe to occur
94 somewhere on Earth in the future (Christoudias et al., 2014).

95

96 **2. Areas targeted by decontamination**

97 In November 2011, the Japanese government adopted the *Act on Special Measures Concerning the Handling of Pollution by Radioactive Materials* (Japanese Ministry of the Environment, 2011a) in order
98 to reduce the impact of radioactive substances from the FDNPP accident on human health and the
99 environment (Yasutaka and Naito, 2016). In support of this Act, decontamination guidelines were
100 released by the Japanese Ministry of Environment in December 2011 and updated in 2013. These
101 guidelines outlined the methods for surveying and quantifying the levels of contamination and the way
102 to prepare these areas targeted for remediation (Japanese Ministry of the Environment, 2013). A
103 decontamination roadmap (*Policy for Decontamination in the Special Decontamination Area*) was
104 implemented in January 2012 under the direct supervision of the Japanese government.
105

106 According to the decontamination roadmap, the remediation programme had to be implemented in
107 'special areas' where targets were set for the exposure of the public to external dose rates in order for
108 residents to return to their day-to-day lives (Yasutaka and Naito, 2016). Achieving pre-accident
109 radiation levels is not the objective, rather the effectiveness of decontamination will ultimately depend
110 upon the land use and the air dose of each particular area. Two zones were delineated with different
111 strategies for remediation (Figure 2). First, Special Decontamination Zones (SDZ) are areas located
112 within a 20-km radius of the FDNPP or areas where the cumulative dose one year after the accident
113 was expected to exceed 20 mSv yr⁻¹. SDZs occur in 11 municipalities (1117 km²) where residents were
114 evacuated after the FDNPP accident in 2011. The central government of Japan is responsible for
115 remediation works in SDZs. Second, Intensive Contamination Survey Areas (ICAs) refer to 102
116 municipalities from eight Prefectures with ambient dose rates exceeding 0.23 µSv h⁻¹, designated as
117 ICAs by the Ministry of Environment on December 28, 2011 (Mori et al., 2017). The area of the ICAs is
118 eight times greater than the SDZ (Yasutaka and Naito, 2016). In particular, the decontamination
119 methods and target areas for remediation in the ICAs differ from those of the SDZ with
120 decontamination activities for the ICAs conducted by local governments with support from the central
121 government. In total, the SDZs and ICAs cover a surface area of 8953 km² with a population that was
122 not evacuated after the accident of ~1.7 million (Yasutaka and Naito, 2016).

123 In the literature, there is debate regarding the need to initiate decontamination so quickly after the
124 FDNPP accident (e.g., Yasutaka et al., 2013a). Delaying decontamination could allow for the natural
125 decay of radioisotopes and thus significantly lower the costs of achieving radiation exposure targets.
126 For example, Munro (2013) estimated that the optimal delay for implementing remediation activities
127 was in the range of 3–10 years after the accident, with an optimal delay of 8.8 years.

128

129

130
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## 3. Decontamination Strategies and their Cost Effectiveness

The effectiveness of decontamination was assumed to strongly vary depending on the remediation method and the initial radiation dose rates prior to decontamination. Different remediation techniques were proposed depending on the land use and the zone (i.e., SDZ vs. ICA). Yasutaka et al. (2013a) and Yasutaka et al. (2013b) compared the impact of four scenarios of decontamination, including two very unlikely options (i.e., minimal and maximal scenarios), in terms of effectiveness and cost according to the results of demonstration tests conducted by JAEA. These results were updated in a more recent publication (Yasutaka and Naito, 2016). Only the two scenarios following the guidelines provided by the Japanese government are assessed in this review. As such, the results of both the minimal and maximal remediation options are therefore not discussed. In the first scenario, 5 cm of topsoil was removed from 50% of agricultural land in the SDZ where ¹³⁷Cs concentrations exceed 5000 Bq kg⁻¹, and replaced with a 5-cm layer of 'clean' soil (measure A1; Table 2). In the remaining 50% of agricultural land with ¹³⁷Cs concentrations below 5000 Bq kg⁻¹, topsoil was interchanged with subsoil (measure A3). Ploughing with zeolite and potassium (measure A4) was adopted for agricultural land in ICAs where the annual additional effective dose exceeded 1 mSv yr⁻¹. In the second scenario, measure A1 was applied to all cultivated land. Similar measures (e.g. Table 2) were included in both scenarios to decontaminate forested areas, roads and houses. The total decontamination cost for implementing these remediation measures varied between 2–5.1 trillion JPY (~16–41 billion EUR), with 1.3–2 trillion JPY (~10–16 billion EUR) for the SDZ and 0.7–3.1 (~6–25 billion EUR) for the ICAs. Although the area where decontamination has been implemented in the ICAs (922–3330 km²) covers a surface 3 to 11 times larger than that of SDZ (295 km²), the decontamination costs for the SDZ and ICAs are in the same order of magnitude.

The decontamination program includes a variety of other activities on top of the actual on-site remediation works, including the transport of waste, the volume reduction of waste along with the temporary, the interim, and the final storage of decontamination waste and removed soil in containers. Depending on the set of measures implemented in the field, the cost of the remediation works will therefore be highly variable. A synthesis of the unit costs for waste management and storage is provided in Table 3 (Yasutaka and Naito, 2016). As shown by Yasutaka et al. (2013b), the quantity of waste generated when decontaminating agricultural land varies considerably depending on the decontamination method used. Consequently, differences in the quantity of waste generated resulted in large differences between agricultural land decontamination methods and the costs associated with storage containers, temporary storage sites and interim storage facilities.

According to the latest available figures from the Japanese Ministry of the Environment (2019b) at the end of 2018, the volume of soil waste generated in the SDZ was 9,100,000 m³ with a remediation cost of approximately 1.5 trillion JPY (~12 billion EUR). In the ICAs, the latest figures available for March 2018 showed that 7,900,000 m³ of waste soil were produced with a remediation cost of approximately 1.4 trillion JPY, equivalent to ~11 billion EUR (Japanese Ministry of the Environment, 2019a).

## 4. Strategies for decontamination in various environments, and their effectiveness

In general, owing to the strong and nearly irreversible bond of radiocesium to fine soil particles, the majority of FDNPP derived ¹³⁷Cs is stored within the topsoil (i.e. the top 5 cm) in undisturbed soils (Lepage et al., 2014; Matsunaga et al., 2013; Takahashi et al., 2015; Mishra et al., 2015; Matsuda et al., 2015). Mishra et al. (2015) reported that for these undisturbed soils, the vertical migration of radiocesium down the soil profile was slower in forest soils compared to grassland soils. In disturbed soils, anthropogenic activities may increase the depth migration of radiocesium down the soil profile
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176 (Lepage et al., 2015; Matsunaga et al., 2013). For example, Lepage et al. (2015) illustrated that 90% of the FDNPP derived radiocesium was homogeneous throughout the tilled soil layer in cultivated soils.
177 Endo et al. (2013) reported that radiocesium concentrations were not depth dependent in cultivated soils (i.e. paddy fields) whereas they declined exponentially in uncultivated soil. Both Sakai et al. (2014b) and Tanaka et al. (2013) also demonstrated that radiocesium from the FDNPP accident was measureable at 15cm depth in rice paddy fields. As illustrated by Koarashi et al. (2012), the penetration of radiocesium in the soil differed depending on both the land use and the physicochemical properties of the soil (e.g., bulk density, clay content and organic matter content). However, remediation strategies consisting in removing the top 5 cm layer of the soil should have been effective as cultivation or other human activities that may have led to the redistribution of radiocesium with depth after the accident were prohibited in the main fallout impacted region.
185
186

187 Soil/farmland decontamination

188 Different strategies were carried out in Japan to decontaminate soil in farmland, either removing the contaminated layer of soil or through the sowing of plants having the capacity of extracting and concentrating radiocesium from the soil. There are few publications in international journals regarding the potential or effectiveness of the latter strategy (e.g. Parediuk et al., 2015). Among the few available studies, Kobayashi et al. (2014) grew thirteen plant species from three families (Asteraceae, Fabaceae, and Poaceae) in shallow and deeply cultivated fields where the 0–8 cm and 0–15 cm soil layers were respectively ploughed. The variation in plough depth was expected to reflect the impact of different contact zones between the root systems and radiocesium in the soil. Overall, 29 to 225 Bq kg⁻¹ dry weight of ¹³⁷Cs were found in the plants, corresponding to transfer factors ranging from 0.019 to 0.13 (geometric mean (GM), 0.057) for plants growing in shallow soils, and from 0.022 to 0.13 (GM 0.063) for plants growing in deeper soils (Kobayashi et al., 2014). The authors found that none of their tested plant species resulted in a significant decrease in radiocesium in soil likely because of the strong fixation of ¹³⁷Cs to clay particles. This result was confirmed by Yamashita et al. (2014) who showed that 99 wild plants grown in paddy and upland fields had a very low phytoextraction efficiency. Tamaoki et al. (2016) reached the same conclusions, although they suggested Kochia (Bassia scoparia) as a potential candidate for phytoremediation although its efficiency in removing ¹³⁷Cs would require numerous cultivation rounds.
205
206

Accordingly, given the low efficiency of phytoremediation, the main remediation strategy consists of removing the surface layer of soils with the majority of radiocesium. The effectiveness of this strategy was examined by Sakai et al. (2014a) in Kawamata Town. Approximately 5-10 cm of the surface soil was removed from one rice paddy by heavy machinery, whereas a nearby paddy field was not decontaminated and used as control plot. Both of these paddies then were ploughed and planted with rice. Five surface soil samples (0-5 cm) were collected after decontamination and prior to ploughing on June 12, 2011. Thereafter five soil cores (20 cm depth) were collected on July 13, 2012 at 3 m intervals across both rice paddy fields. In 2011, the accumulation of radiocesium in the 0-5 cm surface layer of the soil in the decontaminated paddy field (170±64 Bq kg⁻¹) was lower than the control rice paddy field (2231 ±64 Bq kg⁻¹). However, the ¹³⁷Cs concentration of the surface soil layer in the decontaminated rice paddy field (753±62 Bq kg⁻¹) was significantly higher in 2012 than in 2011. This result suggests that radiocesium is likely redistributed through the rice paddy field irrigation and drainage networks. The authors concluded that the redistribution of soil within the paddy fields may decrease the effectiveness of decontamination. A lack of replicates was outlined by the authors and prevented them to finally conclude on the effectiveness of surface removal for decontamination (Sakai et al., 2014a). In contrast, Kurokawa et al. (2019) observed a 80% decrease in ¹³⁷Cs activities after 2017
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222 decontamination in cultivated land of Tomioka Town, showing the efficiency of this remediation strategy.

223
224
225 Another study was conducted in experimental paddy fields located ~40 km from the FDNPP (Wakahara et al., 2014). Two plots were established: a paddy field where the top 5–10 cm of soil was removed
226
227 before cultivation and a control paddy. The ¹³⁷Cs soil inventory measured 3 months after the FDNPP
228
229 accident was approximately 200,000 Bq m⁻². However, after decontamination, this inventory decreased to 5000 Bq m⁻². Suspended sediment and ¹³⁷Cs fluxes were measured in the outflow of the paddy fields after puddling (i.e., the mixing of soil and water before planting rice) and they were 11.0
230
231 kg and 630,000 Bq (1240 Bq m⁻²) respectively in the control paddy, versus 3.1 kg and 24,800 Bq (47.8
232
233 Bq m⁻²) in the decontaminated paddy. After irrigation, 5.5 kg of particles and 51,900 Bq (102 Bq m⁻²) of ¹³⁷Cs were discharged from the control plot, whereas 70 kg of suspended sediment and 165,000 Bq
234
235 (317 Bq m⁻²) of ¹³⁷Cs were discharged from the remediated field. This 3-fold higher export of ¹³⁷Cs from the decontaminated paddy was likely explained by the supply of contamination from upper paddy
236
237 fields, which remained connected to the remediated field. This result highlights the importance of remediation strategies focusing on the entire catchment scale.

238
239 Although this practice has not been specifically investigated in the literature, decontamination of
240 farmland in the Fukushima fallout-impacted region was not limited to the removal of the 5-cm topsoil
241 layer concentrating the radiocesium. After this first step, a layer of crushed granite, extracted from
242 local quarries dedicated to decontamination, is used to replace the removed soil layer (Evrard et al.,
243 2019). The entire soil profile consisting of the residual initial soil (in depth) and this crushed granite
244 layer (on top) is then thoroughly mixed to prepare the soil for recultivation with the objective being to
245 further dilute the residual radiocesium activities in the soil (Figure 3).
246

246
247 Other studies investigated the impact of remediation works on the radiocesium levels measured in sediment transiting the river networks draining the main radioactive pollution plume. Evrard et al. (2016) modelled the progressive dilution of radiocesium concentrations measured in sediment following decontamination works. They demonstrated a 90% decrease of the contribution of upstream contaminated soils to sediment transiting the coastal plains of the Mano and Niida Rivers between 2012 and 2015. Furthermore, Osawa et al. (2018) monitored the radiocesium concentrations in suspended sediment collected in two tributaries of the Mano and Niida Rivers from 2013 and 2016. They also attributed a decrease in the ¹³⁷Cs concentrations observed in 2016 to the decontamination efforts completed in 2015 in the local catchments.
248
249
250
251
252
253
254
255
256

256
257
River channel decontamination

258 Riverside parks and playgrounds are popular across Japan. Sediment containing high quantities of
259 radionuclides may also accumulate near these parks and playgrounds in river channels and floodplains
260 following flooding events (Saegusa et al., 2016). However, sediment deposition is highly
261 heterogeneous both horizontally and vertically across floodplains. Furthermore, sediment deposited
262 in the river channel may be resuspended during subsequent flood events. In these conditions, the
263 common decontamination guidelines (i.e. removing the uppermost layer; Table 2) are difficult to
264 implement effectively.
265

265 Nishikiori and Suzuki (2017) investigated this challenge in the 13-km² Kami-Oguni River catchment, a tributary of the Abukuma River, in the Fukushima Prefecture. Decontamination of a 170-m long and 8 to 13-m wide river section isolated from the floodplain with 2-m high concrete dikes was studied, as the roads located on top of the banks were used by children to go to school. First, all the plants were
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removed from the channel. Then, the top 5-cm layer of sediment was excavated from the dike slopes and planted with turf. Afterwards, sediment was removed from the channel, and the removal depth (between 15-35 cm) was locally adjusted depending on the vertical distribution of radiocesium measured using a NaI scintillation detector before, immediately after, and then three months after the remediation campaign. In addition, sediment samples were collected along transects at various depths in the floodplain and analysed with coaxial germanium detectors. Radiocesium contamination strongly varied with depth, depending on changes in the mud versus sand fractions, the former being enriched in radiocesium. Radiocesium concentration also varied across the channel, depending on the local flow velocity, which varied depending on the flood magnitude, the plant density and the microtopography. Before decontamination, air dose rates 1 cm above the ground varied between 0.2–1.99 µSv h⁻¹, demonstrating the heterogeneity of contamination. After remediation, the contamination levels decreased by a factor of approximately 2, from a mean of 0.78 (±0.41) µSv h⁻¹ before decontamination to 0.34 (±0.15) µSv h⁻¹ after decontamination at 1 cm above the ground. However, Nishikiori and Suzuki (2017) underlined the risk associated with the potential deposition of contaminated material originating from upstream landscapes during subsequent flood events.

### Forest decontamination

The guidelines for the decontamination of forested areas in the Fukushima Prefecture (Table 2) indicate that only those areas lying within 20 m of houses should be targeted for remediation (Yasutaka and Naito, 2016) (Figure 4). Although the remediation in forests has not been a priority for the Japanese authorities during the early post-accidental phase, pilot studies were conducted to quantify the potential effectiveness of wider remediation programmes. Ayabe et al. (2017) investigated the impact of local-scale decontamination including the removal of the litter layer, the superficial soil layer, and the understorey in a secondary mixed forest with a cover of bamboo grass, *Sasa nipponica*, as understorey located in Kawamata Town. Although the total ¹³⁷Cs contamination in soil and litter was reduced by ~20% after decontamination compared to an adjacent untreated area, the radioactive contamination levels returned to their initial level four months after the completion of remediation works. This was likely due to the occurrence of a torrential rainfall event and the supply of contaminated foliage to the ground by litterfall. These results suggest that the removal of the litter and superficial soil layers in a contaminated forest may have limited effectiveness.

In another study by Lopez-Vicente et al. (2018), several different forest decontamination practices were compared through the monitoring of ¹³⁷Cs contamination in soil and leaf samples in 10 plots installed in the evacuation zone, 16 km to the southwest of FDNPP, between May 2013 and July 2015 (i.e. 27 months monitoring). Four potential forest remediation strategies were assessed. First, the combination of tree thinning and litter removal provided the best results to reduce ¹³⁷Cs export (350–380 Bq m⁻² day⁻¹), followed by the application of tree thinning only (163–174 Bq m⁻² day⁻¹). Clearcutting and litter removal provided limited results (92–104 Bq m⁻² day⁻¹), with higher ¹³⁷Cs export rates than those observed from the control plots (52 Bq m⁻² day⁻¹). Finally, plots where tree matting was conducted had lower ¹³⁷Cs export rates (19–25 Bq m⁻² day⁻¹) than control plots. Overall, the decreasing trend in radiocesium concentrations measured in the plot outflow was high in 2013, moderate in 2014 and low in 2015 owing to the vegetation recovery after the countermeasures.

309

### 5. Impact of decontamination on dosimetry

Two parameters are assessed before authorizing evacuees to return home: the prevalent dose rate and the cumulative dose. Importantly, background radiation levels need to be incorporated into this assessment. In the Fukushima Prefecture, background does rates before the FDNPP accident were
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314 estimated to be ~0.04-0.05 mSv h⁻¹ (National Institute of Advanced Industrial Science and Technology, 2011).

315
316 Individual external radiation doses (mSv day⁻¹) may not be directly related to outdoor air doses (mSv day⁻¹) as people do not spend 24 hours a day outside. When people are inside, the distances from the sources of radiation are greater and walls generate a shielding effect (IAEA, 2000). In Japan, when the Ministry of the Environment estimated daily individual external effective dose rates, it was assumed that people spent 8 hours outdoors and 16 hours indoors, with the indoor air dose rate being 40% of the outdoor air dose rate (Japanese Ministry of the Environment, 2013). Based on these assumptions, the external radiation dose rate is 60% of the air dose rate. Several researches have estimated external conversion coefficients according based on data provided by the Ministry of the Environment (Yasutaka and Naito, 2016).

325 Figure 5 compares the annual and individual dose rates that the global population may be exposed to
326 in order to help facilitate a comparison with levels in the FDNPP fallout-impacted region. In Japan, a
327 long-term dosimetric target of 1mSv yr⁻¹ was adopted by the Nuclear Emergency Response
328 Headquarters. Accordingly, a guidance value of 0.23 µSv h⁻¹ was proposed to achieve the target by
329 implementing decontamination measures. In particular, areas with ambient dose rates exceeding this
330 value were defined as ICAs. This guidance value is based on a simplified deterministic model assuming
331 that inhabitants again spend 8 hours outdoors and 16 hours indoors (i.e. a shielding factor of 0.4) per
332 day and that the contribution of natural radiation is 0.04 mSv h⁻¹ (IAEA, 2013). According to Mori et al.
333 (2017), this model has three main challenges. First, the same behavioural pattern is assumed for the
334 entire population. Second, the radiation exposure is assumed to be uniform. Third, conservative
335 assumptions are adopted when converting the ambient dose into an effective dose. For instance, the
336 time spent outside is assumed to be 8 hours, which is more than anticipated for the majority of the
337 population and likely results in an overestimation of the actual measured doses (Nomura et al., 2015).

338 Although this approach is effective for the immediate post-accidental context, more sophisticated
339 approaches are required to estimate doses over the longer term. Therefore, a probabilistic method
340 that accounts for spatial variations (i.e., houses, workplaces, and other environments) of the
341 contamination and for inter-populational variations (i.e., indoor workers, outdoor workers,
342 pensioners) in behavioural patterns was developed by Mori et al. (2017). For this approach, the 95th
343 percentile doses for outdoor workers were above 1 mSv yr⁻¹ in 25 of the 59 municipalities in Fukushima
344 Prefecture (1–35 mSv yr⁻¹). In particular, the doses to more than 90% of the outdoor workers in Okuma
345 town, Futaba town, Tomioka town, Namie town, and litate village were over 1 mSv yr⁻¹. Furthermore,
346 the 95th percentile doses for indoor workers were above 1 mSv yr⁻¹ in Okuma town, Futaba town,
347 Tomioka town, Namie town, and litate village. If people return home in these municipalities, it is
348 possible that they would be exposed to doses exceeding 1 mSv yr⁻¹ for all population groups. However,
349 the results indicate that the same behavioural patterns and contamination levels should not be
350 assumed for all inhabitants nor all municipalities. Based on the different behaviour of the local
351 population, the 95th percentile doses of indoor workers and pensioners in 53 of the 59 municipalities
352 were below the dosimetric target of 1 mSv yr⁻¹ (0.026–0.73 mSv yr⁻¹) (Mori et al., 2017). Radiation dose
353 rates were also measured among different types of workers having professional activities in the village
354 of Kawauchi where the annual doses of foresters (range: 0.7–1.9 mSv yr⁻¹) were not significantly higher
355 than those of farmers (0.7–1.5), builders (0.6–1.5), office workers (0.5–1.5) and unemployed
356 individuals (0.5–1.7). In contrast, decontamination workers (0.5–7.1) were found to have significantly
357 higher dose rates (Orita et al., 2017).

358 The workers involved in decontamination activities were often directly exposed to internal irradiation
359 through inhalation, which is much more difficult to measure than the external irradiation. Accordingly,
<figure><img src="image_17.png" /></figure>

<figure><img src="image_18.png" /></figure>

eighty-three people who worked in highly contaminated areas where surface ¹³⁷Cs deposition density was over 100 kBq m⁻² were enrolled in a study (Tsubokura et al., 2013). Using a database on internal exposure from the Hirata Central Hospital in Fukushima Prefecture, data were compiled on age, gender, body weight, equipment used in decontamination activity, total working period, duration between the final working day and the day of an examination, and ¹³⁴Cs and ¹³⁷Cs body burden. Hirata Central Hospital was also equipped with a permanent whole body counter with detection limits of 300 Bq per individual for both ¹³⁴Cs and ¹³⁷Cs measurements following a 2-min scan. The levels of internal radiocesium exposure among all the decontamination workers were below the detection limits. No other radionuclides besides natural ⁴⁰K were detected. No acute health problems had been reported. However, levels of external exposure were not assessed, as individual data on dose rates were not available. This study suggests that the resuspension of radioactive materials may cause a minimal internal contamination during decontamination works (Yamaguchi et al., 2012). Other studies calculated that radiation doses from internal exposure were marginal (Hayano et al., 2013; Tsubokura et al., 2015). As such, remediation efforts should be concentrated on reducing the external exposure of the local population.

According to the decontamination scenarios described in section 3, the reduction in annual individual additional Effective Dose (ED) for all decontamination scenarios was 1666 person-Sv for the SDZ and 876-1245 person-Sv for the ICAs (Yasutaka and Naito, 2016). Despite the higher reduction rate achieved in the SDZ compared to the ICAs, they remained in the same order of magnitude although the decontamination efficiencies were very different in both areas. This result may be directly attributed to the differences in population density in SDZ and ICAs, with 90,000 inhabitants living in SDZs in 2010 versus approximately 1.5 million inhabitants living in ICAs areas exposed to over 1 mSv yr⁻¹. This strong dependence of ED on population densities may lead the authorities to concentrate their remediation efforts in the most densely populated areas. The results obtained also depend on the effectiveness of these decontamination programmes. For instance in ICAs, where approximately 1 million inhabitants reside in areas exposed to 1–5 mSv yr⁻¹, the reduction in annual individual additional ED was much larger in those areas where the full decontamination scenario would be implemented.

From the aforementioned research on river channel decontamination, the external radiation dose was calculated for paths along the river used by children to go to school and the nearby playgrounds used for outdoor activities incorporating an adapted time of exposition (35 h yr⁻¹ for commuting and 24 h yr⁻¹ for outdoor activities) (Nishikiori and Suzuki, 2017). After decontamination of the river channel, radiation dose rates decreased by a factor of approximately 2. These authors stated that the optimal strategy should be to reduce the annual individual additional ED as much as possible for the whole population, while also decreasing high dose individuals (Yasutaka and Naito, 2016). Indeed, the authorities should not only assess the cost-benefit effectiveness of remediation programmes, they must also consider ethical and social costs (Oughton et al., 2004).

396

## 6. Treatment of decontamination waste (soil, vegetation)

### Waste management

The management of waste generated by the succession of catastrophes that affected the Fukushima Prefecture in March 2011 has proved to be very complex, as debris derived from the earthquake, the tsunami and the radioactive materials were mixed, resulting in a very atypical mixture of 'disaster waste' (Shibata et al., 2012). Earthquake and tsunami-associated waste had elevated levels of metals and metalloids (e.g., mercury, arsenic and lead), with the tsunami waste being particularly difficult to manage.
<figure><img src="image_19.png" /></figure>

<figure><img src="image_20.png" /></figure>

Regarding waste contaminated with ¹³⁷Cs, the final objective is to bring radiocesium to the solution phase and then enrich it, to reduce it to the smallest possible volume. In the Fukushima Prefecture, the radiocesium concentrations found in the disaster waste are lower than other alkali metals. Therefore, the treatment methods require approaches that help concentrate ¹³⁷Cs (Parajuli et al., 2016a). The reduction of solid waste volume can be achieved through compaction or incineration. For organic waste (i.e. forest litter, weeds, wood, or tree branches from contaminated areas), incineration ('thermal treatment') is traditionally preferred (IAEA, 2003, 2006) as it reduces the volume of waste by several orders of magnitude (Parajuli et al., 2013). The problem is that this 'thermal treatment' may enrich contaminants and the Japanese legislation has a 8000 Bq kg⁻¹ radionuclide threshold for placing waste in landfills (Japanese Ministry of the Environment, 2011b).

Accordingly, waste contaminated with radionuclide levels between 8000 Bq kg⁻¹ and 100,000 Bq kg⁻¹ needs to be disposed in designated landfills equipped with radiation level and leachate monitoring as well as a treatment system in order to control the potential release of radioisotopes into the environment (Parajuli et al., 2013). Therefore, either specially designed landfills need to be constructed or pre-treatment methods need to be designed to remove radionuclides from the waste. This issue is crucial as the construction of temporary storage sites and interim storage facilities were estimated to account for 50% of the overall cost of decontamination. For example, transport, storage and administrative costs were estimated to represent a cost of 1.55–2.12 trillion JPY (~12.4–17 billion EUR) for the decontamination scenarios complying with the guidelines of Japanese authorities (Yasutaka and Naito, 2016). Furthermore, securing routes and locations for transporting more than 20 million tonnes of decontamination waste and removed soil that were generated to the interim storage facilities remains a major challenge. Nevertheless, assessing the management and storage of low-concentration radioactive cesium-containing soil and methods for using controlled landfill sites may lead to a significant reduction in the amount of material requiring transport.

The combustible waste generated through decontamination was initially stored at temporary storage facilities (Figure 6). The volume of this waste was to be reduced by incineration, and the incineration ash was transferred to interim storage facilities. In 2013, the Japanese Ministry of Environment made a plan stating that incineration ashes with high ¹³⁷Cs concentrations and leachable characteristics should be stored in concrete shielded structures facilities. After being transferred to interim storage facilities, incombustibles (e.g., soil) were planned to be stored at soil storage facilities in the interim storage facilities (Yasutaka and Naito, 2016). The interim storage facilities are to be built in the areas neighbouring the FDNPP (i.e., in Okuma and Futaba municipalities), while the temporary storage sites were planned to be built in six municipalities in the SDZ (i.e., from North to South: litate, Minamisoma, Katsurao, Namie, Tomioka and Naraha municipalities).

Contaminated soil removed by decontamination works is transported to an interim storage facility where flammable decontamination waste (DW) is incinerated or melted to reduce its mass and volume. Depending on its radiocesium content, this waste is either stored at an interim storage facility or disposed in a leachate-controlled type of landfill site (Fujiwara et al., 2017). The total surface area of the interim storage facilities in Futaba and Okuma municipalities is planned to cover ~1600 ha, and by February 2019, a contract was already established between Japanese authorities and landowners for ~70% of the land required for storage. Soil storage operations started in October 2017 in Okuma and in December 2017 in Futaba. By March 2019, ~2.5 million m³ of waste soil had already been transported from the temporary storage facilities distributed across all the remediated area to these two interim storage facilities (Japanese Ministry of the Environment, 2019a). All the soil waste is planned to be transported to the Okuma and Futaba sites by the end of 2021 (Japanese Ministry of the Environment, 2019b). The final disposal of this decontamination waste should take place outside of
<figure><img src="image_21.png" /></figure>

<figure><img src="image_22.png" /></figure>

451 the Fukushima Prefecture, within 30 years after the opening of the interim storage facilities (i.e.,
452 ~2047).

453 Incineration

454 The temperature used in the furnaces used for incineration of radioactive waste is similar to that used
455 in the plants treating municipal waste (870-882°C). The incinerators for radioactive waste are
456 radiation-controlled areas, with workers following protocols in accordance with the Ordinance on
457 Prevention of Ionizing Radiation Hazards (Act No. 134 of the 2015 amendment of Law No. 41 of the
458 Japanese Ministry of Labour in 1972). The heavier particles are collected at the bottom of the furnace,
459 generating the so-called bottom ash (BA), while the lighter particles pass to a bag-filter where the
460 temperatures are kept lower (250-300°C) and where the so-called fly ash (FA) and the vaporised
461 cesium are collected (Figure 7). The exhaust gas is filtered to trap the residual fine particles, generating
462 several types of FA. Measurements made on incineration products since 2015 showed that BA and FA
463 are produced with similar levels of radiocesium, both with low radiocesium leachability (<1%) (Fujiwara
464 et al., 2017). Radiocesium levels in the exhaust gases were found to be lower than method detection
465 limits (Parajuli et al., 2013).

466 Incineration ash treatment

467 The chemical form and the leachability of radiocesium depends on the type of waste incinerated.
468 Results observed for three different types of ash samples suggest that ¹³⁷Cs along with other alkali
469 metals in wood bark and household garbage ashes, originated from burnable materials, were mostly
470 washed out with water even at ambient temperatures. However, municipal sewer sludge was
471 different, with potential ¹³⁷Cs elution only occurring under very specific conditions (i.e., with acid
472 treatment and under high temperatures). Acid treatment at high temperatures was found to be
473 inappropriate for treating wood bark and household garbage ashes because of the generation of a Ca
474 excess leading to gypsum formation and complexifying the subsequent treatment process (Parajuli et
475 al., 2013).

476 Soil recycling

477 As 22 million m³ of decontamination soil (i.e. 90% of the total) and incineration ash waste (10%) is
478 expected to be produced through remediation of the fallout impacted region, recycling may be
479 instrumental for reducing this volume (Takai et al., 2018). The Japanese Ministry of Environment
480 developed a policy to separate decontamination soil into low- and high-activity soils, the former being
481 'recycled' in public projects. In these uses, decontamination soil will be used for the basic structure
482 and will be covered by uncontaminated soil or concrete. In theory, the unconditional 'clearance level'
483 defined by IAEA for the use of recycled material is fixed to 100 Bq kg⁻¹ for radiocesium. However, as
484 disaster waste was found with higher ¹³⁷Cs levels, the Japanese Ministry of Environment decided that
485 those materials with radiocesium levels up to 3000 Bq kg⁻¹ can be reused at a minimum depth of 30
486 cm underground (reference level assessed for recycling of concrete for the road subbase course). For
487 decontamination soil recycling, the radioactivity level had to be reanalysed for a different type of
488 engineering structures (deterministic estimation of radiation dose rates). The corresponding level of
489 radiocesium concentrations in the soil was estimated to 6000 Bq kg⁻¹. To confine doses to levels below
490 10 µSv yr⁻¹ based on the derived radioactivity level, an additional layer of soil slope protection of 40
491 cm or more was needed. Accordingly, the Japanese Ministry of Environment determined the maximum
492 radioactivity level to be 6,000 Bq kg⁻¹ for embankments covered with 50 cm uncontaminated soil.
493 Overall, the recycling of decontaminated soil is limited to civil engineering structures in public projects,
494 such as road embankments and coastal levees. Takai et al. (2018) evaluated the associated additional
<figure><img src="image_23.png" /></figure>

<figure><img src="image_24.png" /></figure>

495 doses to workers and the public using these structures and demonstrated that additional dose rates
496 would remain below the 1 mSv yr⁻¹ threshold corresponding to 6000 Bq kg⁻¹.

497 In Japan, contaminated wastes are disposed under the standard of 8,000 Bq kg⁻¹. The volume of
498 decontamination soil having a radioactivity concentration of 8,000 Bq kg⁻¹ or below is estimated to be
499 approximately 10 million m³, which corresponds to half of the total amount of decontamination soil
500 generated. The radioactivity concentration of 8,000 Bq kg⁻¹ will decrease to 6,000 Bq kg⁻¹ in 5 years.
501 Therefore, more than half of the total decontamination soil should become recyclable in at least 5
502 years. Through the use of pre-treatment activities, such as classification processing, even more
503 decontaminated soil may become recyclable in the non-too distant future (Takai et al., 2018).

504 Soil remediation

505 Remediation of contaminated soil based on a hot acid treatment was tested for the two most common
506 soil groups found in Fukushima (Parajuli et al., 2016b): Cambisols (i.e. brown forest soils) and Andisols
507 (i.e. soils developed on volcanic ash). Although this method was shown to be effective for the former
508 soil type, this was not the case for the latter. In particular, lime must be added to treat Andisols which
509 must be mixed with untreated and uncontaminated soil prior to being reused for cultivation.
510 Furthermore, to avoid the transfer of residual radiocesium to plants, additives such as zeolite or
511 Prussian blue adsorbents need to be incorporated into the Andisols. The problem associated with this
512 strategy is that, through their ageing, zeolites may increase ¹³⁷Cs exchangeability with potassium and
513 accelerate ¹³⁷Cs transfer to the cultivated plants over longer time periods (Yamaguchi et al., 2019).
514 These restrictions illustrate the difficulty of finding alternatives to the storage of decontamination soil
515 waste in interim facilities.

516

517 7. Perspectives for future research

518 The total estimated decontamination cost would exceed 16 trillion JPY (~128 billion EUR) if all forested
519 areas exposed to radiation dose rates exceeding 1 mSv yr⁻¹ were decontaminated. However,
520 decontaminating all of the forested areas would not result in a major ED reduction for the average
521 inhabitant (Yasutaka and Naito, 2016). As almost 70% of the surface area of Fukushima Prefecture is
522 covered with forests (Hashimoto et al., 2012) and forestry is a significant economic activity in the
523 region, future research should prioritize investigating radiocesium dynamics in these regions. In
524 particular, the biological cycling of ¹³⁷Cs in forests has now been affected by the decomposition of litter
525 where radiocesium was concentrated shortly after the FDNPP accident (Koarashi et al., 2012).
526 Furthermore, the local population in rural areas of the Fukushima Prefecture enjoy ‘satoyama’, or the
527 collection of vegetation, including mushrooms, edible wild plants, and firewood from forested
528 landscapes (Prand-Stritzko and Steinhauser, 2018; Nihei, 2016). In addition, approximately 1800
529 workers are employed by the forest industry in the region (Yasutaka and Naito, 2016). For many of the
530 local inhabitants, the forest, the satoyama, and its harvest are inseparable from their daily lives.

531 Forest sources were also shown to deliver a significant proportion of contaminated material to the
532 river systems draining the fallout-impact region. The analysis of deposited particulate matter collected
533 in three fallout-contaminated coastal catchments between November 2012 and November 2014
534 demonstrated that forest sources supplied a mean of 17 % (standard deviation, SD, 10 %) of the
535 sediment transiting these river systems (Laceby et al., 2016). Huon et al. (2018) obtained similar results
536 through the analysis of sediment cores collected between November 2014 and April 2015 in a dam
537 reservoir draining fallout-impacted cultivated and forested landscapes, with the latter supplying a
538 mean of 27% (SD, 6%) of the material deposited in the lake. These conclusions were validated through
539 an analysis of a larger number of sediment samples (n=400) collected in coastal river systems in the
<figure><img src="image_25.png" /></figure>

<figure><img src="image_26.png" /></figure>

540 Fukushima region over a longer time period (from November 2011 to November 2017) where a mean of 24% (SD, 21%) of the material transiting these systems was modelled to be derived from forested landscapes (Evrard et al., 2019). Cumulatively, these results demonstrate that forested landscapes represent a potential long-term source of particulate contaminated matter that likely will require diligent management for the foreseeable future.

545 In cultivated landscapes where the remediation activities were concentrated, the main question is whether or not to restart agricultural production. The removal of the topsoil layer concentrating the radiocesium, the replacement of this material with crushed granite extracted from local quarries and the final mixing of the entire profile to prepare the soils for re-cultivation raises several important questions. For example, to what extent will the residual radiocesium in the soil be transferrable to the plants cultivated on these soils? How will the crushed granite, which was homogenized into the soil, affect the soils fertility? Recent research showed that potassium fertilization is required to maintain productivity when restarting cultivation after decontamination (Kurokawa et al., 2019). Indeed, as it was demonstrated in the current literature review, the reopening of the region after the completion of remediation activities represents a unique situation in history, coupled with unprecedented challenges that require further ongoing investigations.

550
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555 Although previous dosimetric studies demonstrated that currently the internal exposure of both the local population and the decontamination workers remains minimal, both internal and external exposures of these groups should be studied over longer temporal periods to help understand long-term impacts of this and potentially other nuclear accidents on exposed population groups. More research is also required to understand the fate and dynamics of other longer-lived radionuclides in the Fukushima region including radiocarbon (Paterne et al., 2018; Povinec et al., 2016; Xu et al., 2016), plutonium and uranium isotopes (Jaegler et al., 2018; Zheng et al., 2013; Steinhauser, 2014) as they may be persistent in the environment even though many were emitted only at the trace and ultra-trace levels.

565 **Conclusions**

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The quick and early decision of the Japanese authorities to decontaminate FDNPP fallout impacted landscapes was unprecedented. Decontamination activities were rapidly implemented in agricultural and residential areas covering a surface of ~9000 km². These remediation activities produced ~20 million m³ of soil waste in less than 6 years (2013–2019) with an approximate cost of 3 trillion JPY (~24 billion EUR). The strategy of removing the surface layer of the soil concentrating ¹³⁷Cs was shown to be effective in cultivated land when the strategy was applied at a catchment scale to avoid the supply of mobilized contamination from the headwaters. The main current challenges are associated with the treatment and the transport of this waste to the interim storage facilities for the next ~30 years that are being built near the FDNPP. The re-cultivation of the soils after decontamination also raises several concerns. In particular, more information is required regarding soil fertility after decontamination and the potential transfer of the residual ¹³⁷Cs to the plants cultivated on decontaminated fields.

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The risks of internal and external radiation dose exposures of the decontamination workers and the local population to exceed the target of 1mSv yr⁻¹ appeared to be low during the early post-accidental phase. However, dosimetric monitoring programmes should be carried out to confirm this result over the longer term, particularly after local population returns to the region. Furthermore, as ~75% of the surface exposed to the highest ¹³⁷Cs fallout levels in the Fukushima Prefecture are covered with forests where decontamination was not implemented, the perennial contribution of radiocesium to the river systems draining these mountainous, forested landscapes exposed to typhoons should be investigated. The behaviour and the dynamics of longer-lived radionuclides such as plutonium isotopes
<figure><img src="image_27.png" /></figure>

<figure><img src="image_28.png" /></figure>

585 should also be studied in the future as they may persist in the environment for long timescales even
586 though they were emitted at trace and ultra-trace levels.

587

588 Acknowledgements

589 This research was funded by the AMORAD project (ANR-11-RSNR-0002), supported by the French
590 National Research Agency (ANR, Agence Nationale de la Recherche). The support of CNRS (Centre
591 National de la Recherche Scientifique, France) and JSPS (Japan Society for the Promotion of Science)
592 in the framework of the Franco-Japanese collaboration project framework (PRC, CNRS-JSPS) is also
593 gratefully acknowledged.

594

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729
730
731
732

Koarashi, J., Atarashi-Andoh, M., Matsunaga, T., Sato, T., Nagao, S., and Nagai, H.: Factors affecting vertical distribution of Fukushima accident-derived radiocesium in soil under different land-use conditions, The Science of the total environment, 431, 392-401, 10.1016/j.scitotenv.2012.05.041, 2012.

Kobayashi, D., Okouchi, T., Yamagami, M., and Shinano, T.: Verification of radiocesium decontamination from farmlands by plants in Fukushima, Journal of plant research, 127, 51-56, 10.1007/s10265-013-0607-x, 2014.

Kobayashi, S., Shinomiya, T., Ishikawa, T., Imaseki, H., Iwaoka, K., Kitamura, H., Kodaira, S., Kobayashi, K., Oikawa, M., Miyashiro, N., Takashima, Y., and Uchihori, Y.: Low ¹³⁴Cs/¹³⁷Cs ratio anomaly in the north-northwest direction from the Fukushima Dai-ichi Nuclear Power Station, Journal of environmental radioactivity, 178-179, 84-94, 10.1016/j.jenvrad.2017.07.023, 2017.

Konoplev, A., Golosov, V., Laptev, G., Nanba, K., Onda, Y., Takase, T., Wakiyama, Y., and Yoshimura, K.: Behavior of accidentally released radiocesium in soil-water environment: Looking at Fukushima from a Chernobyl perspective, Journal of environmental radioactivity, 151 Pt 3, 568-578, 10.1016/j.jenvrad.2015.06.019, 2016.

Kurokawa, K., Nakao, A., Tsukada, H., Mampuku, Y., and Yanai, J.: Exchangeability of ¹³⁷Cs and K in soils of agricultural fields after decontamination in the eastern coastal area of Fukushima, Soil Science and Plant Nutrition, 1-8, 10.1080/00380768.2019.1622402, 2019.

Laceby, J. P., Huon, S., Onda, Y., Vaury, V., and Evrard, O.: Do forests represent a long-term source of contaminated particulate matter in the Fukushima Prefecture?, Journal of environmental management, 183, 742-753, 10.1016/j.jenvman.2016.09.020, 2016.

Lepage, H., Evrard, O., Onda, Y., Patin, J., Chartin, C., Lefèvre, I., Bonté, P., and Ayrault, S.:

Environmental mobility of ¹¹⁰mAg: lessons learnt from Fukushima accident (Japan) and potential use for tracking the dispersion of contamination within coastal catchments, Journal of environmental radioactivity, 130, 44-55, 2014.

Lepage, H., Evrard, O., Onda, Y., Lefèvre, I., Laceby, J. P., and Ayrault, S.: Depth distribution of cesium-137 in paddy fields across the Fukushima pollution plume in 2013, Journal of Environmental Radioactivity, 147, 157-164, 2015.

Lopez-Vicente, M., Onda, Y., Takahashi, J., Kato, H., Chayama, S., and Hisadome, K.: Radiocesium concentrations in soil and leaf after decontamination practices in a forest plantation highly polluted by the Fukushima accident, Environmental pollution, 239, 448-456, 10.1016/j.envpol.2018.04.045, 2018.

Matsuda, N., Mikami, S., Shimoura, S., Takahashi, J., Nakano, M., Shimada, K., Uno, K., Hagiwara, S., and Saito, K.: Depth profiles of radioactive cesium in soil using a scraper plate over a wide area surrounding the Fukushima Dai-ichi Nuclear Power Plant, Japan, Journal of Environmental Radioactivity, 139, 427-434, 2015.

Matsunaga, T., Koarashi, J., Atarashi-Andoh, M., Nagao, S., Sato, T., and Nagai, H.: Comparison of the vertical distributions of Fukushima nuclear accident radiocesium in soil before and after the first rainy season, with physicochemical and mineralogical interpretations, Science of the Total Environment, 447, 301-314, 2013.

Mishra, S., Arae, H., Sorimachi, A., Hosoda, M., Tokonami, S., Ishikawa, T., and Sahoo, S.: Distribution and retention of Cs radioisotopes in soil affected by Fukushima nuclear plant accident, Journal of Soils and Sediments, 15, 374-380, 10.1007/s11368-014-0985-2, 2015.

Mori, A., Takahara, S., Ishizaki, A., Iijima, M., Sanada, Y., and Munakata, M.: Assessment of residual doses to population after decontamination in Fukushima Prefecture, Journal of environmental radioactivity, 166, 74-82, 10.1016/j.jenvrad.2016.06.023, 2017.
<figure><img src="image_31.png" /></figure>

<figure><img src="image_32.png" /></figure>

733 Munro, A.: The economics of nuclear decontamination: assessing policy options for the management of land around Fukushima dai-ichi, Environmental Science & Policy, 33, 63-75, 10.1016/j.envsci.2013.04.008, 2013.

734

735 10.1016/j.envsci.2013.04.008, 2013.

736 Nagao, S., Kanamori, M., Ochiai, S., Tomihara, S., Fukushi, K., and Yamamoto, M.: Export of <sup>134</sup>Cs and <sup>137</sup>Cs in the Fukushima river systems at heavy rains by Typhoon Roke in September 2011, Biogeosciences, 10, 6215-6223, 10.5194/bg-10-6215-2013, 2013.

737 <sup>134</sup>Cs and <sup>137</sup>Cs in the Fukushima river systems at heavy rains by Typhoon Roke in September 2011, Biogeosciences, 10, 6215-6223, 10.5194/bg-10-6215-2013, 2013.

738

739 Nakao, A., Ogasawara, S., Sano, O., Ito, T., and Yanai, J.: Radiocesium sorption in relation to clay mineralogy of paddy soils in Fukushima, Japan, The Science of the total environment, 468-469, 523-529, 10.1016/j.scitotenv.2013.08.062, 2014.

740

741 529, 10.1016/j.scitotenv.2013.08.062, 2014.

742 Nakao, A., Takeda, A., Ogasawara, S., Yanai, J., Sano, O., and Ito, T.: Relationships between Paddy Soil Radiocesium Interception Potentials and Physicochemical Properties in Fukushima, Japan, J Environ Qual, 44, 780-788, 10.2134/jeq2014.10.0423, 2015.

743 Nakao, A., Takeda, A., Ogasawara, S., Yanai, J., Sano, O., and Ito, T.: Relationships between Paddy Soil Radiocesium Interception Potentials and Physicochemical Properties in Fukushima, Japan, J Environ Qual, 44, 780-788, 10.2134/jeq2014.10.0423, 2015.

744 Qual, 44, 780-788, 10.2134/jeq2014.10.0423, 2015.

745 National Institute of Advanced Industrial Science and Technology: Geochimical Map of the Sea and Land of Japan, 2011.

746

747 Nihei, N.: Monitoring inspection for radioactive substances in agricultural, livestock, forest and fishery products in Fukushima prefecture, in: Agricultural Implications of the Fukushima Nuclear Accident, Springer, Tokyo, 11-21, 2016.

748

749 Accident, Springer, Tokyo, 11-21, 2016.

750 Nishikiori, T., and Suzuki, S.: Radiocesium decontamination of a riverside in Fukushima, Japan, Journal of environmental radioactivity, 177, 58-64, 10.1016/j.jenvrad.2017.06.005, 2017.

751

752 Nomura, S., Tsubokura, M., Hayano, R., Furutani, T., Yoneoka, D., Kami, M., Kanazawa, Y., and Oikawa, T.: Comparison between direct measurements and modeled estimates of external radiation exposure among school children 18 to 30 months after the Fukushima nuclear accident in Japan, Environ Sci Technol, 49, 1009-1016, 10.1021/es503504y, 2015.

753

754 exposure among school children 18 to 30 months after the Fukushima nuclear accident in Japan, Environ Sci Technol, 49, 1009-1016, 10.1021/es503504y, 2015.

755

756 Orita, M., Fukushima, Y., Yamashita, S., and Takamura, N.: The Need for Forest Decontamination: For the Recovery of Fukushima, Radiation protection dosimetry, 175, 295-296, 10.1093/rpd/ncw301, 2017.

757

758 2017.

759 Osawa, K., Nonaka, Y., Nishimura, T., Tanoi, K., Matsui, H., Mizogichi, M., and Tatsuno, T.:

760 Quantification of dissolved and particulate radiocesium fluxes in two rivers draining the main radioactive pollution plume in Fukushima, Japan (2013–2016), Anthropocene, 22, 40-50, 2018.

761

762 Oughton, D., Forsberg, E. M., Bay, I., Kaiser, M., and Howard, B.: An ethical dimension to sustainable restoration and long-term management of contaminated areas, Journal of environmental radioactivity, 74, 171-183, 10.1016/j.jenvrad.2004.01.009, 2004.

763

764

765 Parajuli, D., Tanaka, H., Hakuta, Y., Minami, K., Fukuda, S., Umeoka, K., Kamimura, R., Hayashi, Y.,

766

767 decontamination of radioactive cesium enriched ash, Environ Sci Technol, 47, 3800-3806, 10.1021/es303467n, 2013.

768

769 Parajuli, D., Kitajima, A., Takahashi, A., Tanaka, H., Ogawa, H., Hakuta, Y., Yoshino, K., Funahashi, T.,

770 Yamaguchi, M., Osada, M., and Kawamoto, T.: Application of Prussian blue nanoparticles for the radioactive Cs decontamination in Fukushima region, Journal of environmental radioactivity, 151 Pt 1, 233-237, 10.1016/j.jenvrad.2015.10.014, 2016a.

771

772 1, 233-237, 10.1016/j.jenvrad.2015.10.014, 2016a.

773 Parajuli, D., Suzuki, Y., Sato, M., Takahashi, A., Tanaka, H., and Kawamoto, T.: Assessment of the measures for the extraction or fixation of radiocesium in soil, Geoderma, 267, 169-173, 10.1016/j.geoderma.2016.01.001, 2016b.

774

775 10.1016/j.geoderma.2016.01.001, 2016b.

776

777 K.: Modification of <sup>137</sup>Cs transfer to rape (Brassica napus L.) phytomass under the influence of soil microorganisms, Journal of environmental radioactivity, 149, 73-80, 2015.

778

779 Paterne, M., Evrard, O., Hatté, C., Laceby, P. J., Nouet, J., and Onda, Y.: Radiocarbon and radiocesium in litter fall at Kawamata, ~ 45 km NW from the Fukushima Dai-ichi nuclear power plant (Japan), Journal of Radioanalytical and Nuclear Chemistry, 10.1007/s10967-018-6360-9, 2018.

780

781

782 Povinec, P. P., Liong Wee Kwong, L., Kaizer, J., Molnár, M., Nies, H., Palcsu, L., Papp, L., Pham, M. K.,

783 and Jean-Baptiste, P.: Impact of the Fukushima accident on tritium, radiocarbon and radiocesium
<figure><img src="image_33.png" /></figure>

<figure><img src="image_34.png" /></figure>

784 levels in seawater of the western North Pacific Ocean: A comparison with pre-Fukushima situation,
785 Journal of environmental radioactivity, 10.1016/j.jenvrad.2016.02.027, 2016.

786 Prand-Stritzko, B., and Steinhauser, G.: Characteristics of radiocesium contaminations in mushrooms
787 after the Fukushima nuclear accident: evaluation of the food monitoring data from March 2011 to
788 March 2016, Environmental Science and Pollution Research, 25, 2409-2416, 2018.

789 Saegusa, H., Ohyama, T., Iijima, K., Onoe, H., Takeuchi, R., and Hagiwara, H.: Deposition of
790 radiocesium on the river flood plains around Fukushima, Journal of environmental radioactivity, 164,
791 36-46, 10.1016/j.jenvrad.2016.04.020, 2016.

792 Sakai, M., Gomi, T., Nunokawa, M., Wakahara, T., and Onda, Y.: Soil removal as a decontamination
793 practice and radiocesium accumulation in tadpoles in rice paddies at Fukushima, Environmental
794 pollution, 187, 112-115, 10.1016/j.envpol.2014.01.002, 2014a.

795 Sakai, M., Gomi, T., Nunokawa, M., Wakahara, T., and Onda, Y.: Soil removal as a decontamination
796 practice and radiocesium accumulation in tadpoles in rice paddies at Fukushima, Environmental
797 Pollution, 187, 112-115, 2014b.

798 Shibata, T., Solo-Gabriele, H., and Hata, T.: Disaster waste characteristics and radiation distribution as
799 a result of the Great East Japan Earthquake, Environ Sci Technol, 46, 3618-3624,
800 10.1021/es300055m, 2012.

801 Steinhauser, G.: Fukushima's forgotten radionuclides: a review of the understudied radioactive
802 emissions, Environ Sci Technol, 48, 4649-4663, 10.1021/es405654c, 2014.

803 Steinhauser, G., Brandl, A., and Johnson, T. E.: Comparison of the Chernobyl and Fukushima nuclear
804 accidents: a review of the environmental impacts, The Science of the total environment, 470-471,
805 800-817, 10.1016/j.scitotenv.2013.10.029, 2014.

806 Stohl, A., Seibert, P., Wotawa, G., Arnold, D., Burkhart, J. F., Eckhardt, S., Tapia, C., Vargas, A., and
807 Yasunari, T. J.: Xenon-133 and caesium-137 releases into the atmosphere from the Fukushima Dai-
808 ichi nuclear power plant: determination of the source term, atmospheric dispersion, and deposition,
809 Atmospheric Chemistry and Physics, 12, 2313-2343, 10.5194/acp-12-2313-2012, 2012.

810 Takahashi, J.,amura, K., Suda, T., Matsumura, R., and Onda, Y.: Vertical distribution and temporal
811 changes of ¹³⁷Cs in soil profiles under various land uses after the Fukushima Dai-ichi Nuclear Power
812 Plant accident, Journal of environmental radioactivity, 139, 351-361, 2015.

813 Takai, S., Sawaguchi, T., and Takeda, S.: Dose Estimation in Recycling of Decontamination Soil
814 Resulting From The Fukushima NPS Accident For Road Embankments, Health Phys, 115, 439-447,
815 10.1097/HP.0000000000000904, 2018.

816 Tamaoki, M., Yabe, T., Furukawa, J., Watanabe, M., Ikeda, K., Yasutani, I., and Nishizawa, T.:

817 Comparison of Potentials of Higher Plants for Phytoremediation of Radioactive Cesium from
818 Contaminated Soil, Environmental Control in Biology, 54, 65-69, 10.2525/ecb.54.65, 2016.

819 Tanaka, K., Iwatani, H., Takahashi, Y., Sakaguchi, A., Yoshimura, K., and Onda, Y.: Investigation of
820 Spatial Distribution of Radiocesium in a Paddy Field as a Potential Sink, PLoS ONE, 8,
821 10.1371/journal.pone.0080794, 2013.

822 Tsubokura, M., Nihei, M., Sato, K., Masaki, S., Sakuma, Y., Kato, S., Sugimoto, A., Nomura, S.,
823 Matsumura, T., Miyazaki, M., Hayano, R., Shibuya, K., Kami, M., and Sasaki, T.: Measurement of
824 internal radiation exposure among decontamination workers in villages near the crippled Fukushima
825 Daiichi Nuclear Power Plant, Health Phys, 105, 379-381, 10.1097/HP.0b013e318297ad92, 2013.

826 Tsubokura, M., Kato, S., Morita, T., Nomura, S., Kami, M., Sakaihara, K., Hanai, T., Oikawa, T., and
827 Kanazawa, Y.: Assessment of the Annual Additional Effective Doses amongst Minamisoma Children
828 during the Second Year after the Fukushima Daiichi Nuclear Power Plant Disaster, PloS one, 10,
829 e0129114, 10.1371/journal.pone.0129114, 2015.

830 Wakahara, T., Onda, Y., Kato, H., Sakaguchi, A., and Yoshimura, K.: Radiocesium discharge from
831 paddy fields with different initial scrapings for decontamination after the Fukushima Dai-ichi Nuclear
832 Power Plant accident, Environ Sci Process Impacts, 16, 2580-2591, 10.1039/c4em00262h, 2014.

833 Xu, S., Cook, G. T., Cresswell, A. J., Dunbar, E., Freeman, S. P., Hou, X., Jacobsson, P., Kinch, H. R.,

834 Naysmith, P., Sanderson, D. C., and Tripney, B. G.: Radiocarbon Releases from the 2011 Fukushima
835 Nuclear Accident, Scientific reports, 6, 36947, 10.1038/srep36947, 2016.
<figure><img src="image_35.png" /></figure>

<figure><img src="image_36.png" /></figure>

836 Yamaguchi, N., Eguchi, S., Fujiwara, H., Hayashi, K., and Tsukada, H.: Radiocesium and radioiodine in soil particles agitated by agricultural practices: field observation after the Fukushima nuclear accident, The Science of the total environment, 425, 128-134, 10.1016/j.scitotenv.2012.02.037, 2012.

839 Yamaguchi, N., Hikono, A., and Saito, T.: Effects of zeolite and vermiculite addition on exchangeable radiocaesium in soil with accelerated ageing, Journal of environmental radioactivity, 203, 18-24, 10.1016/j.jenvrad.2019.02.011, 2019.

842 Yamashita, J., Enomoto, T., Yamada, M., Ono, T., Hanafusa, T., Nagamatsu, T., Sonoda, S., and Yamamoto, Y.: Estimation of soil-to-plant transfer factors of radiocesium in 99 wild plant species grown in arable lands 1 year after the Fukushima 1 Nuclear Power Plant accident, Journal of plant research, 127, 11-22, 10.1007/s10265-013-0605-z, 2014.

846 Yasunari, T. J., Stohl, A., Hayano, R. S., Burkhart, J. F., Eckhardt, S., and Yasunari, T.: Cesium-137 deposition and contamination of Japanese soils due to the Fukushima nuclear accident, Proceedings of the National Academy of Sciences of the United States of America, 108, 19530-19534, 10.1073/pnas.1112058108, 2011.

850 Yasutaka, T., Iwasaki, Y., Hashimoto, S., Naito, W., Ono, K., Kishimoto, A., Yoshida, K., Murakami, M., Kawaguchi, I., Oka, T., and Nakanishi, J.: A GIS-based evaluation of the effect of decontamination on effective doses due to long-term external exposures in Fukushima, Chemosphere, 93, 1222-1229, 10.1016/j.chemosphere.2013.06.083, 2013a.

854 Yasutaka, T., Naito, W., and Nakanishi, J.: Cost and effectiveness of decontamination strategies in radiation contaminated areas in Fukushima in regard to external radiation dose, PloS one, 8, e75308, 10.1371/journal.pone.0075308, 2013b.

857 Yasutaka, T., and Naito, W.: Assessing cost and effectiveness of radiation decontamination in Fukushima Prefecture, Japan, Journal of environmental radioactivity, 151 Pt 2, 512-520, 10.1016/j.jenvrad.2015.05.012, 2016.

860 Yoshimura, K., Onda, Y., Sakaguchi, A., Yamamoto, M., and Matsuura, Y.: An extensive study of the concentrations of particulate/dissolved radiocaesium derived from the Fukushima Dai-ichi Nuclear Power Plant accident in various river systems and their relationship with catchment inventory, Journal of environmental radioactivity, 10.1016/j.jenvrad.2014.08.021, 2014.

864 Yoshimura, K., Onda, Y., and Wakahara, T.: Time Dependence of the 137Cs Concentration in Particles Discharged from Rice Paddies to Freshwater Bodies after the Fukushima Daiichi NPP Accident, Environmental science & technology, 50, 4186-4193, 2016.

867 Zheng, J., Tagami, K., and Uchida, S.: Release of plutonium isotopes into the environment from the Fukushima Daiichi Nuclear Power Plant accident: what is known and what needs to be known, Environ Sci Technol, 47, 9584-9595, 10.1021/es402212v, 2013.

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879
<figure><img src="image_37.png" /></figure>

880 **Figures**

881 Figure 1. Evolution of the number of studies published on radiocesium and Fukushima (including or

882 not a reference to decontamination) in the literature between 2011–2018, according to the Scopus

883 search engine.

<figure><img src="image_38.png" /></figure>

884

885

886

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<figure><img src="image_39.png" /><figcaption>Figure 2. Location of the Fukushima Prefecture in Japan (Inset Map) and the location of the Special Decontamination Zones (SDZs) and the Intensive Contamination Survey Areas (ICAs).</figcaption></figure>

901

<figure><img src="image_40.png" /></figure>
<figure><img src="image_41.png" /></figure>

<figure><img src="image_42.png" /></figure>

903 Figure 3. Illustration of the different steps of remediation activities in cultivated land in Fukushima: (a)

904 removal of the 5-cm topsoil layer concentrating most of the radiocesium (November 2013); (b)

905 addition of a crushed granite layer on top of the residual soil profile (May 2014); (c) final mixing of the

906 entire profile to prepare re-cultivation (March 2019). Pictures were taken by the authors in the litate

907 Village.

<figure><img src="image_43.png" /><figcaption>(a)</figcaption></figure>

<figure><img src="image_44.png" /><figcaption>(b)</figcaption></figure>

908

909
<figure><img src="image_45.png" /></figure>

<figure><img src="image_46.png" /></figure>

<figure><img src="image_47.png" /></figure>

910
911
912

<figure><img src="image_48.png" /><figcaption>Figure 4. Illustration of the 20-m buffer zone decontaminated in forested areas in the vicinity of houses. Example from litate Village (Sasu district).</figcaption></figure>

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917
<figure><img src="image_49.png" /></figure>

<figure><img src="image_50.png" /></figure>

918 Figure 5. Comparison of annual and individual radioactive dose rates to which the population may be exposed, based on a compilation of data (Commissariat à l'Energie Atomique et aux Energies
919
920 Alternatives, 2016;Harada et al., 2014).

<figure><img src="image_51.png" /></figure>

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<figure><img src="image_52.png" /></figure>

937 Figure 6. Temporary storage facilities for radioactive waste in litate Village, in the Fukushima

938 Prefecture.

<figure><img src="image_53.png" /></figure>

939

<figure><img src="image_54.png" /></figure>

940

941

942

943
<figure><img src="image_55.png" /></figure>

<figure><img src="image_56.png" /></figure>

944 Figure 7. Simplified diagram showing the functioning of an incineration plant treating decontamination

945 waste in Fukushima, modified after Parajuli et al. (2013) and Fujiwara et al. (2017).

<figure><img src="image_57.png" /></figure>
<figure><img src="image_58.png" /></figure>

Tables

<table><caption>Table 1. Selection of official websites from the Japanese authorities providing information on the remediation works and their impact. (Last access to these websites on March 8, 2019).</caption><thead><tr><td>Authority</td><td>Type of information</td><td>Webpage</td></tr></thead><tbody><tr><td>Fukushima Prefecture</td><td>Environmental restoration</td><td>https://www.pref.fukushima.lg.jp/site/portal-english/list382.html</td></tr><tr><td>Ministry of Environment</td><td>Environmental Remediation</td><td>http://josen.env.go.jp/en/</td></tr><tr><td>Ministry of Economy, Trade and Industry</td><td>Fukushima Today webpage</td><td>http://www.meti.go.jp/english/earthquake/index.html</td></tr><tr><td>Nuclear Regulation Authority</td><td>Monitoring information</td><td>https://radioactivity.nsr.go.jp/en/</td></tr></tbody></table>
<figure><img src="image_59.png" /></figure>

<figure><img src="image_60.png" /></figure>

1 Table 2. Unit costs and effectiveness of decontamination measures implemented in the SDZ and ICAs after Yasutaka and Naito (2016).

2

<table><thead><tr><th>3 Code</th><th>Measure</th><th>Effectiveness range</th><th>Unit cost</th><th>Nb containers/ha</th><th>Target area</th></tr><tr><td>4</td><td></td><td></td><td>10kJPY/ha (EUR)</td><td></td><td></td></tr></thead><tbody><tr><td>5</td><td></td><td></td><td></td><td></td><td></td></tr><tr><td>6</td><td><strong>Agricultural land</strong></td><td></td><td></td><td></td><td></td></tr><tr><td>7</td><td>A1</td><td>Cut weeds/remove 5cm topsoil/cover soil</td><td>0.34 – 0.80</td><td>950 (7600)</td><td>815</td><td>SDZ</td></tr><tr><td>8</td><td>A2</td><td>Cut weeds/remove 5 cm topsoil</td><td>0.34 – 0.80</td><td>625 (5000)</td><td>815</td><td>SDZ</td></tr><tr><td>9</td><td>A3</td><td>Interchange topsoil and subsoil/add zeolite – K</td><td>0.34 – 0.80</td><td>310 (2500)</td><td>0</td><td>SDZ and ICA</td></tr><tr><td>10</td><td>A4</td><td>Ploughing with zeolite and K</td><td>0.21 – 0.50</td><td>33 (265)</td><td>0</td><td>SDZ and ICA</td></tr><tr><td>11</td><td></td><td><strong>Forest</strong></td><td></td><td></td><td></td><td></td></tr><tr><td>12</td><td>F1</td><td>Remove litter and humus</td><td>0.19 – 0.59</td><td>745 (6000)</td><td>530</td><td>SDZ</td></tr><tr><td>13</td><td>F2</td><td>Remove litter</td><td>0.10 – 0.30</td><td>280 (2250)</td><td>260</td><td>ICA</td></tr><tr><td>14</td><td></td><td><strong>Roads</strong></td><td></td><td></td><td></td><td></td></tr><tr><td>15</td><td>R1</td><td>Shot-blasting, cleaning ditches</td><td>0.15 – 0.66</td><td>480 (4000)</td><td>30</td><td>SDZ</td></tr><tr><td>16</td><td>R2</td><td>Cleaning roads and ditches</td><td>0.08 – 0.33</td><td>240/km (2000)</td><td>88</td><td>ICA</td></tr><tr><td>17</td><td></td><td><strong>Buildings</strong></td><td></td><td></td><td></td><td></td></tr><tr><td>18</td><td>B1</td><td>Full decontamination</td><td>0.29 – 0.70</td><td>1750–3500<br>(14,000–30,000)</td><td>150</td><td>SDZ and ICA</td></tr><tr><td>19</td><td></td><td></td><td></td><td></td><td></td><td></td></tr><tr><td>20</td><td>B2</td><td>Local decontamination</td><td>0.15 – 0.35</td><td>125–250<br>(1000–2000)</td><td>11</td><td>ICA</td></tr><tr><td>21</td><td></td><td></td><td></td><td></td><td></td><td></td></tr></tbody></table>
<figure><img src="image_61.png" /></figure>

<figure><img src="image_62.png" /><figcaption>22 Table 3. Unit costs estimated for waste management and storage after Yasutaka and Naito (2016) in the ICAs.</figcaption></figure>

<table><thead><tr><th></th><th>Measure</th><th>Unit cost (JPY)</th><th>Unit cost (EUR)</th></tr></thead><tbody><tr><td>24</td><td>Storage container</td><td>8000</td><td>65</td></tr><tr><td>27</td><td>Transport from decontamination site to temporary storage site</td><td>3100 / container</td><td>25 / container</td></tr><tr><td>28</td><td>Temporary storage site</td><td>20,000 / container</td><td>160 / container</td></tr><tr><td>29</td><td>Transport from temporary storage site to interim storage facility</td><td>3800 – 16,000 / container</td><td>30 – 130 / container</td></tr><tr><td>30</td><td>Treatment at interim storage facility</td><td></td><td></td></tr><tr><td>31</td><td>Combustible volume reduction</td><td>2000 / container</td><td>16 / container</td></tr><tr><td>32</td><td>Storage of combustible incineration residue</td><td>100,000 / container</td><td>800 / container</td></tr><tr><td>33</td><td>Storage of incombustibles</td><td>30,000 / container</td><td>240 / container</td></tr><tr><td>34</td><td></td><td></td><td></td></tr></tbody></table>