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Friday, January 31, 2014

Background Reading in Radiation, Peak Prosperity

Very good summary. I'm gonna borrow some of your analagies in the radiological hazard classes I teach. :-) You might be interested in my Geiger-Müler measurements after Fukushima.

 http://www.ecoreality.org/wiki/Radiation_log
I have some background in metrology, and the methodology may be of interest. Bottom line: you need long counts and long samples. The proper way to do this would be capture a stream and filter it, then read the filter. I alternated outdoor readings with indoor readings, and was puzzled when the indoor readings were higher!
 http://www.ecoreality.org/wiki/Radiation_fallout_plan
I then discovered that my supposed "control" measurements were actually measuring radiation from some dust on old books! Also perhaps of interest is our radiation fallout plan. As Chris points out, the goal is to avoid ingesting contamination.

If Fukushima has taught us anything, its that nuclear power is totally dependent on a functioning electrical grid. A Carrington Event could result in hundreds of Fukushimas around the globe!

 http://news.nationalgeographic.com/news/2011/03/110302-solar-flares-sun-storms-earth-danger-carrington-event-science/

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FROM
http://www.peakprosperity.com/insider/84663/contamination-threat



Yuliyan Velchev/Shutterstock

Fukushima's Legacy: Understanding the Difference Between Nuclear Radiation & Contamination

It's very important
Tuesday, February 11, 2014, 9:55 AM

Are fish from the Pacific safe to eat? What about the elevated background radiation readings detected in Japan, and recently, in California? Are these harmful levels?
Should we be worried? And if so, what should be done about these potential health threats? What steps should we take to protect ourselves?
As many of you know, I'm a scientist by training. In this report, I'll lay out the facts and data that explain the actual risks. I'll start by pointing out that Fukushima-related fears have been overblown as well as heavily downplayed by parties on each side of the discussion.
Much of this stems from ignorance of the underlying science. But some of it, sadly, seems to be purposefully misleading. Again, on both sides.
To assess the true risks accurately, you need to know about the difference between radiation and contamination. The distinction is vital, and, unfortunately, one of the most glossed-over and misused facets of the reporting on nuclear energy.

Starting with the Bottom Line

All of my research and understanding of the risks of radiation at this point indicate that people living on the West Coast of the U.S. or in Hawaii are currently not in danger from the radiation released in the wake of the Fukushima tragedy.
While the background levels are elevated somewhat, those detected so far remain well within what I consider to be a safe zone. However, should there be another accident at the damaged facility leading to the release of another large plume of radioactive matter, then this assessment could, understandably, change.
The exception to this assessment is for those living within a hundred kilometers of Fukushima. For those people, my analysis points to serious risks, especially for those living with a kilometer or two of the coast, extending 100 kilometers in either direction. The details behind my assessment are contained in the full report below.
The intent of this report is to help readers understand the likely implications of the Fukushima situation with more clarity, as well as to provide a useful framework for identifying the risks posed by any future nuclear incidents and what your response to them should be.
The most important takeaway from this analysis should be this: Radiation, itself, is less a threat than most people imagine. But radioactive contamination is an entirely different and far more dangerous beast.
While both deliver a ‘dose’ of radiation, it's contamination especially ingested contamination that has the greatest odds of delivering a concentrated dose to human tissue in a way that can lead to serious acute and/or chronic damage.
The difference between these two will be explained in detail. For those who chose not to read the full report and just want the punchline, it's this: Contamination is the process of acquiring radioactive particles that then become lodged on, or more dangerously in, your body. Do all you can to protect yourself against it.
Should you find yourself nearby during a nuclear accident, your first order of business is to avoid breathing or ingesting any contaminated particulate matter. This usually involves sheltering in place and is when duct tape and plastic sheeting become your best friends. While it may sound silly to use such a dime-store defense against a nuclear hazard, it is in fact both remarkably effective and entirely necessary. Merely keeping you and your family away from the fallout for a matter of 2-3 days, possibly a bit longer depending on conditions, can make an enormous difference in your survival odds.
For now, the levels of radiation that have been detected and reported outside of Japan are between two and three orders of magnitude below what I would personally consider to be worrisome. And there’s no concrete evidence that the bigger concern, contamination, has traveled to countries outside of Japan.
And within Japan, the story takes on its own complexity (just as happened in the areas surrounding Chernobyl), where local wind patterns in the days after the accident created a complex quilt of danger and (relative) safety.
For those who wish to engage with the context and details of the post-Fukushima world, the journey begins by understanding what ‘radiation’ actually is.

Radiation Types

What do we mean when we say 'radiation'? As it turns out, that word can mean any number of things.
You are bathed in radiation every day: from sunlight, radio waves, wi-fi, etc. Some radiation is electromagnetic (in the case of light), and some is composed of particles (matter).
When we hear about ‘radiation’ in the press, what’s typically being referred to are potentially harmful forms of energetic emissions, both electromagnetic and particulate, that can damage biological organisms.
The main distinction between harmful and benign radiation lies in the ability of the radioactive wave or particle to ionize a molecule in your body. Technically, 'ionizing' means "to create an ion," which involves forcibly stripping an electron off a molecule or atom. This leaves the molecule or atom in a charged state (referred to as 'ionic form'), which thus can cause the affected particle to break apart or otherwise not work as it did before.
For example, the hemoglobin in your blood is a very complex molecule. Breaking even one of its internal bonds can completely destroy its ability to carry oxygen.
Every cell in your body is an enormously complex machine with thousands of different molecules each with a crucial function. Wreck enough of these molecules through the process of ionization and the cell dies. Destroy or disrupt the DNA at the center of the cell, and malfunction will result, one dramatic form being the loss of the ability to self-regulate its growth, which we call cancer.
Radioactive substances emit various forms of energy. Some of the energetic releases are in the form of photon waves (such as gamma or X-rays) while some are in the form of actual fast-moving particles (such as alpha and beta particles, and neutrons).
We lump them all together and call them ‘radiation’. But when it comes to their impact on living organisms, not all forms of radiation are created equally. Some are far more effective 'disrupters of life' than others.
The basic types of radiation you would encounter as a consequence of a nuclear accident like Fukushima are:
  • Alpha particles. These are fast moving nuclei of helium, meaning that they consist of two protons and two neutrons. The electron shell is missing, so these are charged particles in search of electrons to strip from some other hapless molecule or atom. In the subatomic world, these are very large particles and so are the most easily stopped. They cannot penetrate even a single sheet of paper or the layer of dead skin cells on the outside of your body. As a result, they are quite easy to protect against with minimal effort. However, we shouldn't take total comfort in this fact. The deadly toxin polonium-210, the one used to kill various enemies of the Russians over the years, emits alpha particles and is quite effective as a poison. The reason for this lies in the fact that, once ingested, it works its damage in close proximity to a person's cells. On the outside of a body, alpha particles bump into already-dead skin cells, so no harmful damage results. On the inside, they careen straight into living cells and are quite damaging.
  • Beta particles. These are electrons that have been ejected through a radioactive decay process (technically, it's when a neutron decays, yielding both a proton and an electron). Beta radiation can penetrate a sheet of paper easily, and it requires something along the lines of an aluminum plate a few millimeters thick to stop it. Beta particles have medium ionizing power and medium penetrating power, but there is a very wide spectrum of potential power intensities, depending on exactly which radioactive substance is emitting the beta particle. One very common radioactive substance found in nuclear plants, tritium, is a beta emitter.
  • Gamma rays. These are high-energy photons with strong penetrating power and high ionizing potential. In the past, they were distinguished from x-rays on the basis of their energy potential, but they are really the same thing (they are both high-energy photons). Although, what we call an x-ray generally carries a lot less energy than a gamma ray. That is, an x-ray is at the low end of the energetic spectrum, while a gamma ray is at the higher end. This is exactly analogous to the difference between visible sunlight and UV rays, which are the radiation (composed of high-energy photons) that burns your skin. Just place gamma rays a lot further along that same spectrum all the way at the point where, instead of being stopped by your underlay of skin, the gamma rays can create an equivalent ‘sunburn’ on tissues all the way through your body. Gamma rays vary in strength and actually occupy a spectrum of energies (not unlike how white light includes the spectrum of all the colors of the rainbow), so we need to know more about the specific gamma rays in question to know how damaging they might be.
  • Neutrons. Neutrons are the bad boys of the radiation story, and are only found as a consequence of a nuclear reaction (controlled or uncontrolled). Their penetrating power is extraordinary, requiring several meters of solid substance to stop them. They work their harm by indirect ionization, which is not unlike a pool ball smashing into a lamp. A typical example would be the capture of a neutron by a hydrogen nucleus consisting of a single proton, which is then ripped away from its position by the kinetic energy contained by the neutron, and then, like our billiard ball, careens about breaking things, ionizing some atoms/molecules, or shattering the bonds between atoms. In terms of biological damage, neutrons are horrific roughly ten times more damaging than beta or gamma radiation on a per-unit-of-energy basis.
Of course, there's a lot of complexity buried within each of these 'buckets' of radiation types, especially given the uncertainty that each bucket has a range of energies associated with it.
To help clarify this, imagine that we're talking about radiation as if it were vehicles traveling on a highway. It's not really possible to predict how destructive it would be to collide with 'a vehicle,' because that answer depends on knowing factors like the vehicle’s size, weight, and speed.
Bumping into a small car traveling slowly in your same direction will be far less damaging than slamming head-on into a large fully-loaded Mack truck going 80 mph.
The way this is technically measured is by the energy that each type of radiation carries, measured in units called 'electron volts' (eV). Think of the eV rating as combining both the speed and the mass of the vehicle we are trying to rank.
To the eV designation, we'll add the scientific shorthand of K for 'kilo' signifying 1,000 and M for Mega signifying 1,000,000. So 1 KeV = 1,000 eV, and 1 MeV = 1,000,000 eV
Along our radiation 'highway,' we find that x-rays carry the least energy and are in the vicinity of 1.2 KeV. They are small, light cars. Think Fiat.
Gamma rays are not a single vehicle type, because they can have energies anywhere from a few KeV all the way up to 25 MeV. They are everything and anything from tiny TR-6s to massive, fully loaded, Peterbilt double trailer trucks traveling 80 mph. For reference, the gamma rays emitted by gesium-137, a very common byproduct of nuclear reactors and a main component of the Fukushima releases, is 700 KeV, hundreds of times more energetic than your typical dentist x-ray, but not nearly the most potent gamma ray you could encounter.
Some common gamma emitters are cesium-137, cobalt-60 and technetium-99. Also, about 10% of the radioactivity of iodine-131 is gamma, the rest is beta (making this is a mixed radioelement).
Alpha particles have very high kinetic energies standing at about 5 MeV. However, they have exceptionally poor penetrating power, so we might think of them as very large steamrollers that can lurch forwards violently, but only for a few feet. If you are right next to it, you're in big trouble, but otherwise you're safe.
In recent years, a potent alpha emitter, polonium-210, was used to assassinate both Yasser Arafat and Russian critic Alexander Litvinenko. Because polonium-210 only emits alpha particles, you could carry it in a glass vial in your pocket and slip though radiation detectors at any facility because none of the alpha particles would make it through the vial wall (and even if they somehow did, they’d be stopped by the fabric of your pants pocket). In fact, you could merrily rub it on your skin and suffer no ill effects.
But if ingested? Just a few milligrams, a speck the size of a small grain of salt, would be sufficient to kill. All those gigantic lurching steamrollers would be positioned right next to your living cells, crashing into them and destroying your tissues one cell at a time.
Common alpha emitters include radium, radon, polonium, uranium, and thorium.
Beta particles are electrons ejected during proton decay, and they travel at high speed. They can range anywhere between 5 KeV and 20 MeV. For our purposes, the isotopes most commonly associated with nuclear reactions are in the range of 19 KeV (tritium) to 600 KeV (iodine-131 and strontium-90) to 2.3 MeV (yttrium-90). So these range from medium-sized cars to tractor-trailers, in our analogy.
Beta particles have medium penetrating power and they can easily get through your skin to the living tissues beneath. Think of them as being able to give you a very harsh sunburn from the outside inwards if you were exposed long enough. Again, their worst effects come if ingested, where they can cause lots of damage.
Some common beta emitters are strontium-90, yttrium-90, iodine-131, carbon-14, and tritium.
Neutrons are a very wide topic, so we'll just talk about them in terms of a nuclear reactor. The moderate to fast neutrons emitted as a product of fission are extraordinarily dangerous and can penetrate lead shields and many meters of concrete. They are most readily stopped by interacting with hydrogen, so water and wax (and human bodies) which contain lots of hydrogen atoms are better at stopping neutrons than concrete.
Neutrons are not part of the radioactive release from Fukushima. They really aren't ever an issue unless you somehow find yourself near an open, uncontained source of fission like inside the containment shell of an operating reactor, or in the vicinity of an exploding nuclear bomb. Then neutrons are a BIG problem.
Of note: In the early stages of the Fukushima meltdown, neutron 'beams' were detected 13 times from outside the reactors. This understandably caused the TEPCO workers a lot of worry and slowed their response efforts. This was a certain indication that there was spontaneous fission happening outside of a sealed containment vessel, something that TEPCO was busily assuring the world had not happened. They were still claiming that the vessels were intact and full of pumped cooling water.
The bottom line is that the topic of radioactivity is complex. If we want to make intelligent decisions, then we need to know which type of radiation we are talking about.
For example, there are folks walking about with mail-order radiation detectors and reporting ‘counts per minute’ readings. But counts of what, exactly? Is each ‘count’ a low-energy beta particle or a high-energy gamma ray? There’s a world of difference between the two.
So we owe it to ourselves to dig into the context before coming to conclusions. To determine how concerned we should be about any new data, we have to translate ‘counts’ of any particle into their potential health effects.

Radiation's Effect on Our Health

Okay, here's the thing most people don't know about radiation: We are surrounded by it and have evolved with it over billions of years. The body can deal with exposure to a certain amount of ionizing radiation without any difficulty at all. Naturally occurring radioactive elements, such as uranium and radon and carbon-14, have been a part of life since the very beginning. Gamma rays rain down from the celestial heavens every day.
So radiation alone is not a cause for concern for me. Even temporary radiation levels that are significantly above my normal background baseline, as much as ten or twenty times, are not a concern of mine as a healthy adult.
But as our vehicle analogy above showed, first we have to know what kind of radiation we are talking about. Is it alpha, beta, or gamma? How much energy is it carrying?
We also need to know about the person being exposed to the radiation. Tolerance levels for what's "safe" will be lower for kids, the old, and the frail.
For these reasons, science has struggled to come up with a universal measurement for the health impact caused by radiation. As a result, we have several different measurement methodologies parked into a few slightly different, but essentially related, scales. Each attempts to combine the acute effects of radiation exposure into a single 'dose' that is a measure of both the intensity and the duration of the exposure.
As mentioned previously, some radiation has the ability to travel right through our bodies entirely without being absorbed. So, the ‘dose’ reading needs to focus on the amount of any specific radiation type that will be absorbed (or stopped) by the body and thereby have opportunity to impact the molecules in that body.
The radiation absorbed dose is measured in Gray, rad, rem, and Sievert.
Rads and Grays are related to each other. One Gray is a huge dose, and the rad just breaks the Grays down into finer units. One Gray = 100 rads (rad stands for Radiation Absorbed Dose). These measure the amount of energy that ionizing radiation imparts to matter. This matter could be anything: a block of cement, or a human.
Sieverts and rems are likewise related. One Sievert = 100 rems, but these are adjusted to provide a measure of the impact of the absorbed dose of ionizing radiation on biological tissue. To equate the two systems, the absorbed dose in Grays or rads is multiplied by a 'quality factor' that is specific to each type of radiation to account for their different biological impacts: the result is Sieverts or rems. Thus, using our vehicle analogy from before, our small sedans get an adjustment factor of 1, while heavier vehicles get an adjustment factor as high as 10-20 times greater.
Based on this table, it's no wonder that polonium-210 is such a devastating radiological poison, because alpha particle get an adjustment factor of 20 (!), making them twice as deadly as fast neutrons, even. But, again, the alpha particles have to be ingested to have that impact, whereas neutrons can travel through ten feet of concrete and still be dangerous.
Keep in mind this table is a huge simplification of a very complicated field of study. For example, it also matters which tissues are being exposed, as they have very different sensitivities to radiation.
However, if we are talking about an episode of external exposure to radiation, like a worker at Fukushima might get, then we care about the Sievert or rem scale:
  • 1 Sievert (or 1 Sv), or 100 rem, will induce nausea and reduce the white blood cell count
  • 5 Sv, or 500 rems, would cause death for 50% of those exposed in a matter of months
  • 10 Sv, or 1,000 rems, is 100% fatal within weeks
The above table leaves out the element of time, so if you are standing near a source of ionizing radiation that is hitting you at the rate of 1 SV per hour, after ten hours you will have received 10 Sv, a fatal dose. If you stand next to that source for an hour you will get nauseous, and destroy some of your white blood cells. If you only stand there for ten minutes, you'll receive something like 100 mS (the maximum yearly allowed dose for U.S. nuclear workers) and likely not feel any adverse effects.
Thus, dose is a function of intensity and time. You may recall seeing the grainy footage of Chernobyl ‘workers’ ducking out from behind cover and racing to move a single wheelbarrow of rubble from point A to point B. In those few seconds, they may have received a lifetime maximum dose of radiation and were (hopefully) sent home after accomplishing that one task.
The average global background radiation is 0.27 microS/hour (that's millionths of a Sievert). If we multiply that number by 24x365, it yields an average yearly dose of 2.4 mS/yr. TEPCO workers are permitted to receive 250 mS/yr, while U.S. nuclear worker standards are 100 mS/yr, which is roughly 25 times greater than background.
The average airport security screening device delivers a dose of 0.25 microS, or the equivalent of a full day's background radiation. If that alarms you, just know that during the actual flight you take, the average exposure is ten times higher than that providing 2.7 microS per hour of flight at cruising altitude, or ten times normal background. So a 5-hour flight at cruising altitude will provide you with a dose of gamma radiation that measures 54 times more than you get at the airport screening itself, or two full days worth of background radiation.
Again, at these levels, I am not even remotely concerned. If there were something to worry about, then the epidemiological data from flight attendants and pilots would have long ago revealed a health concern. That's one reason why I'm not worried about periodic episodes of 10x normal background radiation.
Of course, the Sievert is a very crude scale, developed a long time ago. One might argue that the biological impact of airport screeners and whole-body gamma irradiation might be more subtle and complex due to differences in tissue responses and how the radiation is concentrated on the surface of the skin by airport scanners. All of that remains an open question to me, but not enough of one to concern me.
Still, the point here is that we are surrounded by radiation all the time, and we absorb a yearly dose no matter where we live but Denver-ites get a lot more than people living in Miami due to the altitude (less atmospheric protection from extra planetary gamma arrays).
Here's a link to a super useful graphic that visually shows the Sievert doses of both ordinary life and the Fukushima accident in relation to each other.
Based on this chart, plus all of the information above, even if your background radiation goes up by a factor of ten or twenty, I wouldn't be concerned.

Contamination Is the Real Danger

But radioactive contamination? That's a whole different beast.
By "contamination," I mean ingesting some radioactive isotopes or particles that become lodged in the body somehow. Perhaps it's a small speck of radioactive dust that gets lodged in the lung where it will persist (like coal dust and asbestos do), or perhaps it's a substance that our bodies try to accumulate because it resembles a biologically useful element (as is the case with iodine or strontium).
In Part II: The Contamination Threat, we examine in depth the threats posed by radioactive contamination, including the most prevalent contaminants to be wary of, and the compounding effects of bioaccumulation and biomagnification. One of the most nefarious aspects of contamination is how it uses Nature's processes against itself.
For the record, we are aware of no imminent public health threat from nuclear contamination outside of already-identified "hot zones." But for those who wish to better understand the risks and prudent protection measures related to the real dangers of a similar Fukushima-type event in the future (or an unfortunate escalation of the current Fukushima situation), being forewarned is forearmed.
Click here to access Part II of this report (free executive summary; enrollment required for full access).

Executive Summary

  • The "usual suspects" of dangerous radioactive contamination
  • Recently reported incidents of contamination
  • How bioaccumulation and biomagnification exacerbate the impact of contamination
  • Prudent advice post-Fukushima
If you have not yet read Part I: Fukushima's Legacy: Understanding the Difference Between Radiation & Contamination, available free to all readers, please click here to read it first.

Sources of Radioactive Contamination

As mentioned in Part I, polonium provides an excellent and dramatic example of something that is perfectly safe on the outside of the body and perfectly deadly on the inside. That's the difference between radiation and contamination.
"Radiation, just like with any toxic chemical, is related to dose," said Cham Dallas, a professor and toxicologist at the University of Georgia's Institute for Health Management and Mass Destruction Defense. "If you get a big dose, then you'll die sooner."
And with polonium-210, a dangerous dose can be a matter of micrograms: smaller than a single speck of pepper, he said.
If you ingest polonium-210, about 50% to 90% of the substance will exit the body through feces, according to a fact sheet from Argonne National Laboratory. What is left will enter the bloodstream. About 45% of polonium ingested gets into the spleen, kidneys and liver, and 10% is deposited in the bone marrow.
Radiation poisoning from polonium-210 looks like the end stage of cancer, Dallas said.
Liver and kidney damage ensue, along with extreme nausea and severe headaches. Victims often experience vomiting, diarrhea and hair loss. The alpha particles emitted from the decaying substance get absorbed in the body, which is what causes harm. Death may come in a matter of days, sometimes weeks.
Yes, polonium-210 is highly radioactive a half gram of it in a vial will heat itself up to 500 degrees Celsius all on its own just because of radioactive decay but it is not at all lethal until and unless it is ingested. Once it gets inside, then a fleck the size of a grain of pepper is lethal.
The much-feared plutonium-238 is also an alpha emitter. On the outside of your body it is not much of a problem. Inside it is extraordinarily harmful.
Iodine-131 (I-131) is another "fairly harmless on the outside, but deadly on the inside" sort of substance. Even a vastly sub-lethal dose of I-131 in terms of your whole body load will be damaging if not deadly, because iodine is viewed by your body as a delicious and rare treat, with your thyroid gobbling it up, radioactive or not, and storing it for future use.
As the thyroid does this, the I-131 gets concentrated into a very small body mass where the radioactive load experienced by the thyroid is far higher than any surrounding tissues. At a high enough dose, the thyroid will be destroyed which is a survivable experience, as anybody who's had their thyroid removed can attest.
The real difficulty actually comes with...

Thursday, January 30, 2014

Plutonium -- it Sticks to Your Bones, and Blasts you with Alpha the Strongest Form of Internal Damage

Full credit to

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QUANTITATIVE PLUTONIUM MICRODISTRIBUTION IN BONE TISSUE OF VERTEBRA FROM A MAYAK WORKER

Abstract

The purpose was to obtain quantitative data on plutonium microdistribution in different structural elements of human bone tissue for local dose assessment and dosimetric models validation. A sample of the thoracic vertebra was obtained from a former Mayak worker with a rather high plutonium burden. Additional information was obtained on occupational and exposure history, medical history, and measured plutonium content in organs. Plutonium was detected in bone sections from its fission tracks in polycarbonate film using neutron-induced autoradiography. Quantitative analysis of randomly selected microscopic fields on one of the autoradiographs was performed. Data included fission fragment tracks in different bone tissue and surface areas. Quantitative information on plutonium microdistribution in human bone tissue was obtained for the first time. From these data, quantitative relationship of plutonium decays in bone volume to decays on bone surface in cortical and trabecular fractions were defined as 2.0 and 0.4, correspondingly. The measured quantitative relationship of decays in bone volume to decays on bone surface does not coincide with recommended models for the cortical bone fraction by the International Commission on Radiological Protection. Biokinetic model parameters of extrapulmonary compartments might need to be adjusted after expansion of the data set on quantitative plutonium microdistribution in other bone types in human as well as other cases with different exposure patterns and types of plutonium.
Keywords: plutonium, skeleton, neutron-induced autoradiography

INTRODUCTION

The skeleton is a repository for many metals and radionuclides () and thus is as risk for radiation effects. Plutonium is of particular importance because it is a potent carcinogen and is used in nuclear weapons and nuclear power engineering, as well as other applications. Once plutonium is in the systemic circulation, for example, it is primarily concentrated in the liver and the skeleton in humans (). Epidemiological studies of plutonium personnel cohort show the presence of a reliable correlation between radiation levels from incorporated plutonium and the risk of skeletal malignant tumors (). Furthermore, these plutonium-induced skeletal tumors tend to appear at skeletal sites that differ from naturally occurring tumors (). Other radionuclides that deposit in bone are also associated with skeletal cancers and include 224Ra, 226Ra, 228Ra, 228Th, 249Cf, and 252Cf ().
Neutron-induced autoradiography (NIAR), also called “fission track autoradiography” (FTA), permits the identification and localization of very small amounts of plutonium in biological tissues (). In animal studies, the fission tracks present in the NIARs and the underlying tissue structures can be quantified resulting in estimates of plutonium concentrations and radiation doses to specific anatomical locations. These include structural bone elements and tissue compartments, (i.e. endosteal surfaces, bone tissue, bone marrow) (; ).
The purpose of this report was to present quantitative data on plutonium microdistribution in different areas of human bone tissue. These tissues were obtained from former workers at the Mayak Production Association, Ozyorsk, Russia. This approach should permit investigators to obtain detailed localization and distribution data for plutonium in the human. These data will allow researchers to make skeletal radiation dose assessment more precise, lead to improved radiation safety standards, and further our understanding of radiation-induced human cancers

MATERIALS AND METHODS

The Southern Ural Biophysics Institute (SUBI) Russian Human Radiobiological Tissue Repository (RHRTR) () was the source of biological material for studying plutonium microdistribution in bone tissue. Bone tissue samples were obtained during the autopsy of former workers from the nuclear fuel cycle plant (Mayak) and are stored in separate storage containers in neutral formalin.
For the present study, the biological material of the case (identification number in the repository is 440) with high plutonium body burden (44 kBq) was selected. Personal medical and dosimetric information including radiation history, medical data, autopsy records as well as postmortem radiometry data of organs and tissues is shown in Table 1. The employee worked at the plutonium plant for 7 years as a chemist-technologist and generally had daily contact with relatively soluble plutonium-nitrate compounds. After being diagnosed with chronic radiation sickness, the individual was transferred to another work location for 6.5 years, but had the potential for contact with insoluble plutonium dioxide aerosols. The records indicated exposures to uranium compounds were not likely. The exposures to plutonium-nitrate compounds helps explain the relatively small fraction of plutonium retained in the lungs relative to other organs of this worker (Table 1).
Table 1
Characteristics of RHRTR case #440.

Preparation of samples

A well-preserved sample of thoracic vertebra was obtained for the study. The sample had been stored in neutral formalin for 12 years. The vertebra was selected because the vertebral column is a site with a higher propensity for plutonium-induced sarcomas in experimental animals (; ) and humans (; ). Additionally, the vertebral bodies have a greater content of plutonium per unit bone mass than most other bones (). The tissue samples were dehydrated in ethyl alcohol at a concentration increasing sequentially from 40 to 100%. The dry bones were infiltrated with methyl methacrylate containing benzoyl peroxide as an activator. Infiltration was enhanced by several applications of vacuum to expel the air from the bone. Specimens were placed in a water bath at 37°C, and the temperature held constant until complete polymerization. Sections through the middle of the vertebral bodies were cut using a low-speed bone saw (Isomet, Buehler), polished with aluminum oxide to about 100 μm in thickness and cleaned in ultrapure water. The sections were soaked for 15 min in a 15% sodium borate solution, again rinsed in ultrapure water and allowed to dry in a dust-free environment.

Neutron-induced autoradiography

Neutron-induced autoradiography has an advantage over conventional autoradiography by decreasing the time necessary to attain a sufficient track density. Rather than waiting for a natural decay of the isotope with the registration of the alpha emission on a photographic film or emulsion, NIAR accelerates this by exposing the sections to thermal neutrons that will cause the 239Pu to fission. The fission fragments are registered on plastic detectors, rather than a photographic film or emulsion, as previously described in greater detail (; ). In addition, use of the NIAR is very practical to study plutonium distribution in bone tissue inasmuch as decalcification is not necessary. Decalcification results in plutonium “wash-out” from bone surfaces.
The bone sections were sandwiched between two Lexan polycarbonate detectors (International Plastics, Poulsbo, WA). The sections with their Lexan detectors were placed in a single container fabricated to fit in the port of the nuclear reactor. The container was then irradiated with thermal neutrons at a flux of 8 × 1012 neutron cm−2 s−1 with a total neutron fluence of 9.6 × 1016 neutron cm−2. This was done at the Massachusetts Institute of Technology Nuclear Reactor Laboratory. After the container was removed from the reactor, it was allowed to “cool” for one week to permit the decay of short-lived isotopes generated during the thermal neutron irradiation. The sections and the polycarbonate detectors were then removed and the detectors were placed in a solution of 5 M KOH at 70°C for 8-12 min with constant mild agitation. The detectors were then rinsed with filtered deionized water and allowed to dry. The plutonium fission fragments from the neutron irradiation create holes in the plastic detectors that appear as dark “tracks”. The sodium borate incorporated into the bone during the preparation step creates a subtle, latent bone image on the detectors through fission of the boron atoms. Selected bone sections used for NIAR were then mounted on plastic slides, polished and stained with a modified Giemsa stain for histological examination.

Analysis of autoradiographs

The algorithm proposed by was used for quantitative analysis of the NIARs. For this purpose, detectors were mounted on slides and every fourth viewing field was randomly selected (at magnification x 40). All 8 viewing fields were photographed using a digital camera Olympus DP 11 (Olympus Optical Co, LTD, Japan) and micrographs were printed. The accompanying histological section permitted precise identification of the different structural elements of bone tissue and their boundaries on the autoradiograph. Endosteal surfaces, bone marrow, Haversian canal lumens and bone tissue of cortical and trabecular fractions were quantified. Trabecular bone fraction was observed in all 8 viewing fields, and cortical bone fraction was registered only in 2 viewing fields. Plutonium localization in bone tissue needs to be precisely determined for dosimetric calculations. It was assumed that the ‘ribbon’ outlining the interface of bone-marrow or bone-Haversian canal lumens relates to endosteum area. For track calculation on endosteal surfaces, the width of this ‘ribbon’ was chosen corresponding to a plutonium fission track length. Based on previous data (), this value was 18 μm, and according to data derived in this study a plutonium fission track length was 15 μm, as measured using a digitizing program (AxioVs40,v. 4.7; Carl Zeiss). Therefore, the ‘ribbon’ width specifying endosteum was chosen as 30 μm (15 μm on each side from interface) for calculation of plutonium fission tracks on endosteal surfaces (Fig. 1a-b, 2a-b). However, the observed histological endosteum width was much less. The width of the endosteum was measured in different areas of the histological section using the same digitizing program. The measured mean endosteum width was 6.2 μm (Table 2)
Fig. 1
Structural elements of trabecular bone in (a) histological image, and (b) neutron-induced autoradiograph. M, Marrow; ES, endosteal surface; BV, bone volume. x40.
Fig. 2
Structural elements of cortical bone (a) histological image, and (b) neutron-induced autoradiograph. ES, endosteal surface; BV, bone volume; EH, endosteum of Haversian canals; lumen of Haversian canal is indicated by an arrow. x40.
Table 2
Endosteum width in different compartments of the vertebral specimen.
For identification purposes, the tracks were considered to be straight and not to exceed 20 μm in length (). If a track crossed an interface (e.g., endosteum-marrow), it was assigned to the endosteum, since the probability of its location in endosteum area is much higher than in bone marrow (; ; ). The authors scored the number of tracks in every structural element of bone tissue manually as well as areas and perimeters of these structures.

RESULTS AND DISCUSSTION

According to the biokinetic model of the extrapulmonary compartment of the International Commission on Radiation Protection (), there are cortical and trabecular fractions in skeleton, and each of these is subdivided into bone surfaces, bone volume and bone cavity compartment containing the bone marrow (Fig. 3). Results of plutonium fission fragment tracks scored in the different structural elements of bone tissue, areas of these regions on the sample and values of plutonium fission fragment tracks density in different structural elements are shown in Table 3. The data show that the plutonium distribution in bone tissue is very nonuniform, and this fact conforms to earlier animal studies (; ; ).
Fig. 3
Diagram of the skeletal ICRP model for plutonium ().
Table 3
Number and density of 239Pu fission fragment tracks in different parts of the bone tissue.

Limitations

There were some limitations in this study. First, there is little available data on potential plutonium wash-out from bone tissue fixed in neutral formalin. However, contains a description of an experiment on rats, whose bone tissues during the part of experiments were processed twice with cold 5% trichloroacetic acid. Her work indicated a small portion of the plutonium was washed-out. Thus, if during the period immediately after radionuclide intake, procedures using powerful chemical reagents, there was an 8% wash-out of the nuclide fixed in the bone. It is reasonable to assume that in the case used in this study (Case #440), where the period between the date of plutonium contact and the date of death was more than 20 years, the plutonium was likely firmly fixed in bone tissue and long-term storage in formalin may not have resulted in significant wash-out. However, we cannot exclude the possibility that some translocation of the plutonium may have occurred during the storage period. This would need to be confirmed with an experimental study.
Another limitation is that when scoring, tracks crossing the interface of endosteum-marrow or endosteum-bone were classified as endosteum both for trabecular and for cortical bones, that results in a bias error.
The third challenge is accounting for the background content of natural uranium in the human skeleton. Because uranium is also fissionable, as is plutonium, it can produce fission fragment tracks on autoradiographs that are indistinguishable from the plutonium tracks. The impact of natural uranium content on the quantification of plutonium in bone can be estimated using the neutron physics of these isotopes. Using the analysis outlined in the ratio of fission events due to target nuclei (239Pu) to total fission events can be mathematically determined. Nuclear reactions are first-order irreversible reactions. In the irradiation process, the following competing fission reactions are taking place:
Pu+nfission239,U+nfission238,U+nfission235.
Each reaction rate is described by eqn (1):
ν=Nϕ,
(1)
where v is reaction rate in interactions (cm−3 s−1), ϕ is neutron-flux density (neutron cm−2 s−1), N is atom density (atom cm−3) and σ is microscopic cross-section (barn). For fission processing system with competing first order reactions the overall reaction rate is given here in eqn (2):
ν=iNiσiΦ.
(2)
The concentration of neutrons is several orders of magnitude greater than that of the fissile atoms; thus, we assume constant flux for all species. After some algebraic manipulation the ratio of fission events due to 239Pu to total fission events is given below in eqn (3):
K239Pu=N239PuσNiσi
(3)
The concentration of 238U in human bone tissue is within the range of 100-200 mBq kg−1 (), for people residing in regions with normal natural radiation background (predominantly as a result of entering through the digestive tract). Average concentration of 238U in cortical and trabecular bones on averaged data of United Nations Scientific Committee on the Effects of Atomic Radiation is 150 kBq kg−1 (). On the basis of the ratio 238U and 235U in isotopic composition of natural uranium, averaged concentration of 235U in human bone tissue is 1.08 kBq kg−1.
The content of 239Pu in the skeleton for case #440 was determined to be 20 kBq. Considering that the skeleton mass of adult man is estimated to be about 10.5 kg (), then the content of 239Pu per kilogram of bone tissue for our case was 1.9 kBq kg−1.
Knowing the content of isotopes in the sample as well as their microscopic cross-section on thermal neutrons, it is possible to find the ratio of fission events due to 239Pu, 235U and 238U to total fission events from eqn (3). Results of calculations are presented in Table 4. As can be seen from the table, the fission events due to 239Pu outnumber all other combined fission events. Thus, the contribution of natural uranium content on the number of fission tracks is negligible and most of the tracks are the result of 239Pu fission events.
Table 4
Calculated ratios between fission events from 239Pu, 235U and 238U, and all fission events in the bone sample.

Testing of ICRP model

For the purposes of dosimetry, the bone cavity compartment is assumed to consist entirely of bone marrow in cortical and trabecular fractions (). However, bone marrow in the cortical fraction is essentially non-existent when evaluated using histological criteria (). Haversian canals exist in mature cortical bone and were observed in the cortical bone in this study (Fig 2a). The Haversian canal is also lined with endosteal-like tissues, but the tracks arising from the Haversian surfaces were assigned to the cortical surface compartment.
The data derived from this study were tested against the biokinetic model recommended by the ICRP for assurance of radiation protection standards. The authors considered the ratio between track number in bone volume and track number on bone surface for cortical and trabecular fractions – q(CV)/q(CS) and q(TV)/q(TS), correspondingly.
Using values of volume and surface of bone tissue for cortical and trabecular fractions of the reference man skeleton (Table 5), the authors approximated the data derived from one slide (Table 3) to the whole skeleton. At the same time, for determination of an elementary volume of bone tissue, in which tracks of fission fragments were scored, the area of track scoring was multiplied by the track length (15 μm), except for the endosteum areas (where it was multiplied by the actual endosteum width in the relevant area). Actual values of these parameters for cortical and trabecular fractions were 2.0 and 0.4, correspondingly. These ratios were calculated for this case at the time of death for two scenarios of intake: acute (intake in the first working day) and chronic (uniform intake over the time of contact with radionuclide) using IMBA Professional Plus program, v. 4.0. Calculated and actual values of the ratios between number of decays in the bone volume and number of decays on the bone surface are presented in Table 6. As can be seen from the table, values of parameters coincide for trabecular bone but significantly differ for cortical bone.
Table 5
Values of volume and surface of bone tissue for cortical and trabecular fractions of the skeleton in Standard Man ().
Table 6
Actual and calculated values of ratio between decay number in bone volume and decay number on bone surface for cortical and trabecular fractions.
It should be noted that track density on bone surfaces is an order of magnitude greater then in bone volume for cortical and trabecular fractions according to scoring data of plutonium fission fragment tracks.
Plutonium is initially deposited on bone surfaces but becomes buried and redistributed with time (). Thus the heavy surface concentrations of 239Pu in the NIAR from the worker would suggest a more recent deposition. There are several possible explanations for this. One is that this worker had a very substantial plutonium exposure shortly before death. This was not considered likely considering the employment history of this worker. Another explanation is that plutonium that is recently resorbed and released during bone remodeling may also redeposit onto bone surfaces, as observed in experimental studies (). In this regard, 241Am was observed on vertebral cancellous bone surfaces 11 years after exposure in a human case (). Another explanation is that there was a late in life translocation of 239Pu from the liver. The liver is the other major deposit of plutonium in the body and data from the RHRTR indicates that in workers with a normal health status and from 2-4 decades after their plutonium exposures, the liver contains about 42% of the total residual amount of plutonium in the body with about 50% in the skeleton (). However, when the late-in-life health of the individual is considered, recent data shows that with diseases that affect the liver (such as hepatitis, cirrhosis, metastatic disease or other degenerative diseases), there is a release of plutonium from the liver, some (or perhaps even most) of which appears to be incorporated into the skeleton (). In several studies on the concentrations of plutonium from fallout in humans, the presence of chronic or acute diseases that affect the liver was reported to result in a decreased retention of plutonium in the liver relative to other organs (; ). In the present study, the worker died from a pulmonary cancer with metastatic disease that involved the liver and this may account for some, or perhaps mosts of relative deposition of 239Pu on bone surfaces for this individual.
Moreover, plutonium burden in bone volume is considerably greater than plutonium burden on bone surfaces (Table 6). The data indicates a considerable underestimation of resorption from bone surfaces to bone volume for cortical fraction. It should be noted that these data are preliminary, and they require further development based on of different types of bones and on other cases.

CONCLUSIONS

  1. Quantitative data for plutonium microdistribution in human bone tissue was obtained for the first time on an sample of a thoracic vertebra specimen;
  2. Plutonium distribution in this specimen was very non-uniform. The track density on endosteal surfaces is the next-higher order of magnitude than in the volume of bone tissue, both in cortical and in trabecular fractions;
  3. Actual ratio between the number of 239Pu decays in bone volume and number of 239Pu decays on the bone surface does not coincide with the ICRP recommended values for cortical bone;
  4. It is possible that biokinetic model parameters of extrapulmonary ICRP compartment might need to be adjusted following further studies on quantitative plutonium microdistribution in other human bone types and in individuals with different exposure patterns and scenarios.

Acknowledgments

Sources of support
The Department of Health and Human Services, National Institutes of Health, National Cancer Institute (Grant #R01 CA66759); Russian Federal Medical and Biological Agency (Government Contract # 11.302.06.0).

Footnotes

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REFERENCES

  • Becker K, Johnson DR. Nonphotographic alpha autoradiography and neutron-induced autoradiography. Science. 1970;167:1370–1372. [PubMed]
  • Bruenger FW, Polig E, Jee WSS. Local distribution of 239Pu using digitized images of neutron induced autoradiographs. Radiat Protect Dosim. 1991;35:149–157.
  • Bruenger FW, Smith JM, Atherton DR, Jee WS, Lloyd RD, Stevens W. Skeletal retention and distribution of 226Ra and 239Pu in beagles injected at ages ranging from 2 days to 5 years. Health Phys. 1983;44:513–527. [PubMed]
  • Bukhtoyarova ZM, Nifatov AP. Pu-239 microdistribution and histopathology of dogs’ liver and skeleton after intravenous injection of isotope. In: Moskalev YI, editor. Radioactive isotopes and organism. Medicine; Moscow: 1969. pp. 305–316. (in Russian)
  • Fleischher RL, Price PB, Walker RM. Nuclear Tracks in Solids: Principles and Applications. University of California Press; Berkeley: 1975.
  • Griffith WC, Guilmette RA. Multiparameter analysis of fallout plutonium burdens in human liver. Radiat Protect Dosim. 1991;38:113–119.
  • Ham A, Kormak D. Histology. Mir; Moscow: 1983. (in Russian)
  • International Commission on Radiological Protection . Age-dependent doses to members of the public from intake of radionuclides: Part 2 ingestion dose coefficients. Pergamon Press; Oxford: 1994. ICRP Publication 67.
  • International Commission on Radiological Protection . Basic anatomical and physiological data for use in radiological protection reference values. Pergamon Press; Oxford: 2003. ICRP Publication 89.
  • Jee WSS, Dell RB, Miller LG. High resolution neutron induced autoradiography of bone containing 239Pu. Health Phys. 1972;22:761–763. [PubMed]
  • Kathren RL, McInroy JF, Swint MJ. Actinide distribution in the human skeleton. Health Phys. 1987;52:179–192. [PubMed]
  • Koshurnikova NA, Gilbert ES, Sokolnikov M, Khokhryakov VF, Miller S, Preston DL, Romanov SA, Shilnikova NS, Suslova KG, Vostrotin VV. Bone cancers in Mayak workers. Radiat Res. 2000;154:237–245. [PubMed]
  • Krahenbuhl MP, Slaughter DM. Improving process methodology for measuring plutonium burden in human urine using fission track analysis. J Radioanal Nucl Chem. 1998;230:153–160.
  • Lemberg VK, Bukhtoyarova ZM, Nifatov AP. Plutonium distribution in liver and bones based on histoautoradiography data. In: Lebedinski AV, Moskalev YI, editors. The biological effect of radiation and questions of radioactive isotope distribution. Gosatomizdat; Moscow: 1961. pp. 136–144. (in Russian)
  • Lloyd RD, Miller SC, Taylor GN, Bruenger FW, Jee WSS, Angus W. Relative effectiveness of 239Pu and some other internal emitters for bone cancer induction in beagles. Health Phys. 1994;67:346–353. [PubMed]
  • Lloyd RD, Taylor GN, Angus W, Miller SC, Bruenger FW, Jee WS. Distribution of skeletal malignancies in beagles injected with 239Pu citrate. Health Phys. 1994;66:407–413. [PubMed]
  • Miller SC. Radionuclide-induced skeletal cancers. J Musculoskel Neuron Interact. 2002;2:552–553. [PubMed]
  • Miller SC, Jee WSS, Smith JM, Wronski T. Tissue characteristics of high and low incidence plutonium-induced osteogenic sarcoma sites in life-span beagles. In: Thompson RC, Mahaffey JA, editors. Life-Span Radiation Effects Studies in Animals: What Can They Tell Us? U.S. Department of Energy; Washington DC: 1986. pp. 286–298. CONF-83095.
  • Miller SC, Lloyd RD, Bruenger FW, Krahenbuhl MP, Polig E, Romanov SA. Comparisons of the skeletal locations of putative plutonium-induced osteosarcomas in humans with those in beagle dogs and with naturally occurring tumors in both species. Radiat Res. 2003;160:517–523. [PubMed]
  • Moiseev AA, Ivanov VI. Manual on dosimetry and radiation hygiene. Energoatomizdat; Moscow: 1990. (in Russian)
  • Muksinova KN, Kirillova EN, Zakharova ML, Revina VS, Neta R. A repository of bio-specimens from Mayak workers exposed to protracted radiation. Health Phys. 2006;90:263–265. [PubMed]
  • Mussalo H, Jaakkola T, Miettinen JK. Distribution of fallout plutonium in Southern Finns. Health Phys. 1980;39:245–255. [PubMed]
  • Polig E, Bruenger FW, Lloyd RD, Miller SC. Microdistribution of 239Pu in the beagles skeleton. Health Phys. 1998;75:251–258. [PubMed]
  • Priest ND, Freemont A, Humphreys JAH, Kathren RL. Histopathology and 241Am microdistribution in skeletal USTUR case- 246. Health Phys. 1995;69:330–337. [PubMed]
  • Priest ND, Giannola SJ. 241Plutonium deposition and redistribution in the rat rib. Int J Radiat Biol Relat Stud Phys Chem Med. 1980;37:281–298. [PubMed]
  • Priest ND, Van De Vyver FL. Trace metals and fluoride in bones and teeth. CRC Press; Boca Raton: 1990.
  • Suslova KG, Khokhryakov VF, Tokarskaya ZB, Nifatov AP, Krahenbuhl MP, Miller SC. Extrapulmonary organ distribution of plutonium in healthy workers exposed by chronic inhalation at the Mayak production association. Health Phys. 2002;82:432–444. [PubMed]
  • Suslova KG, Khokryakov VF, Tokarskaya ZB, Nifatov AP, Sokolova AB, Miller SC, Krahenbuhl MP. The effect of state of health on organ distribution and excretion of systemic plutonium in the Mayak workers. Radiat Protect Dosim. 2003;105:229–233. [PubMed]
  • Tseveleva IA. Plutonium burden in protein fractions of rats’ cylindrical bones. Biochemistry. 1960;25:636–639. (in Russian)
  • United Nations Organization . Report to the General Assembly, with annexes. United Nations publication; New York: 1982. Ionized radiation: sources and biological effects. United Nations Scientific Committee on the Effects of Atomic Radiation. E.82.IX.8. 773.
  • Wronski TJ, Smith JM, Jee WSS. The microdistribution and retention of injected 239Pu on trabecular bone surfaces of the beagle: Implications for the induction of osteosarcoma. Radiat Res. 1980;83:74–89. [PubMed]