Thyroid hormone synthesis, Decreased

51-52-5

KNAHARQHSZJURB-UHFFFAOYSA-N

6-Propyl-2-thiouracil

6-Propyl-2 thiouracil (PTU) 4(1H)-Pyrimidinone, 2,3-dihydro-6-propyl-2-thioxo- 2,3-Dihydro-6-propyl-2-thioxo-4(1H)-pyrimidinone 2-Mercapto-4-hydroxy-6-n-propylpyrimidine 2-Mercapto-4-hydroxy-6-propylpyrimidine 2-Mercapto-6-propylpyrimidin-4-ol 2-Thio-4-oxo-6-propyl-1,3-pyrimidine 2-Thio-6-propyl-1,3-pyrimidin-4-one 6-n-Propyl-2-thiouracil 6-n-Propylthiouracil 6-Propyl-2-thio-2,4(1H,3H)pyrimidinedione 6-Propylthiouracil NSC 6498 NSC 70461 Procasil Propacil propiltiouracilo Propycil Propyl-Thiorist Propylthiorit propylthiouracil Propylthiouracile Propyl-Thyracil Prothiucil Prothiurone Prothycil Prothyran Protiural Thiuragyl Thyreostat II URACIL, 4-PROPYL-2-THIO- Uracil, 6-propyl-2-thio-

DTXSID5021209

60-56-0

PMRYVIKBURPHAH-UHFFFAOYSA-N

Methimazole

2H-Imidazole-2-thione, 1,3-dihydro-1-methyl- 1,3-Dihydro-1-methyl-2H-imidazole-2-thione 1-Methyl-1,3-dihydroimidazole-2-thione 1-Methyl-1H-imidazole-2-thiol 1-Methyl-2-mercapto-1H-imidazole 1-Methyl-2-mercaptoimidazole 1-Methyl-4-imidazoline-2-thione 1-Methylimidazole-2(3H)-thione 1-Methylimidazole-2-thiol 1-Methylimidazole-2-thione 2-Mercapto-1-methyl-1H-imidazole 2-Mercapto-1-methylimidazole 2-Mercapto-N-methylimidazole 4-Imidazoline-2-thione, 1-methyl- Basolan Danantizol Favistan Frentirox Imidazole-2-thiol, 1-methyl- Mercaptazole Mercazole Mercazolyl Metazolo Methimazol Methylmercaptoimidazole Metothyrin Metothyrine Metotirin N-Methyl-2-mercaptoimidazole N-Methylimidazolethiol NSC 38608 Strumazol Tapazole Thacapzol Thiamazol thiamazole Thycapzol Thymidazol Thymidazole tiamazol

DTXSID4020820

7439-96-5

PWHULOQIROXLJO-UHFFFAOYSA-N

Manganese

Colloidal manganese Cutaval Manganese element Manganese fulleride Manganese metal alloy Manganese-55 manganeso

DTXSID2024169

7440-47-3

VYZAMTAEIAYCRO-UHFFFAOYSA-N

Chromium

Alpaste RRA 030 Alpaste RRA 050 Chromium element Chromium metal

DTXSID3031022

7440-57-5

PCHJSUWPFVWCPO-UHFFFAOYSA-N

Gold

AGC Micro Britecote Burnish Gold C.I. Pigment Metal 3 Colloidal gold Finesphere Gold W 011 Furuuchi 8560 Gold black Gold element Gold Flake Gold Leaf Keradec Palegold 5550 Perfect Gold Shell Gold Technic 504

DTXSID3064697

7439-97-6

QSHDDOUJBYECFT-UHFFFAOYSA-N

Mercury

Liquid silver Mercure MERCURIC METAL TRIPLE DISTILLED mercurio Mercury element Quecksilber Quicksilver UN 2024 UN 2809

DTXSID1024172

7440-61-1

JFALSRSLKYAFGM-UHFFFAOYSA-N

Uranium

Uranium, isotope of mass 238 238U Element UN 2979 (DOT) Uranium I

DTXSID1042522

7440-38-2

RQNWIZPPADIBDY-UHFFFAOYSA-N

Arsenic

As Arsenic black ARSENIC METAL arsenico Grey arsenic UN 1558

DTXSID4023886

7440-66-6

HCHKCACWOHOZIP-UHFFFAOYSA-N

Zinc

Zn Asarco L 15 C.I. Pigment Black 16 Merrillite NC-Zinc Rheinzink Stapa TE Zinc AT UF (metal) UN 1436 Zinc dust Zinc Dust 3 Zinc Dust 500 mesh Zinc Dust LS 2 Zinc Dust MCS Zinc Flakes GTT ZINC METAL ZINC MOSSY ZINC STRIP ZINC, MOSSY Zincsalt GTT

DTXSID7035012

7429-90-5

XAGFODPZIPBFFR-UHFFFAOYSA-N

AZDRQVAHHNSJOQ-UHFFFAOYSA-N

Aluminum

Aisin Metal Fiber Al 050P-H24 ALC Fine Alcan XI 1391 Almi-Paste SSP 303AR Aloxal 3010 Alpaste 00-0506 Alpaste 0100M Alpaste 0100MA Alpaste 0100M-C Alpaste 0200M Alpaste 0200T Alpaste 0230M Alpaste 0230T Alpaste 0241M Alpaste 0300M Alpaste 0500M Alpaste 0539X Alpaste 0620MS Alpaste 0625TS Alpaste 0638-70C Alpaste 0700M Alpaste 0780M Alpaste 0900M Alpaste 100M Alpaste 100MS Alpaste 100MSR Alpaste 1100M Alpaste 1100MA Alpaste 1100N Alpaste 1100NA Alpaste 1109MA Alpaste 1109MC Alpaste 1200M Alpaste 1200T Alpaste 1260MS Alpaste 1500MA Alpaste 1700NL Alpaste 1810YL Alpaste 1830YL Alpaste 1900M Alpaste 1900XS Alpaste 1950M Alpaste 1950N Alpaste 210N Alpaste 2172EA Alpaste 2173 Alpaste 240T Alpaste 241M Alpaste 417 Alpaste 46-046 Alpaste 4-621 Alpaste 4919 Alpaste 50-63 Alpaste 50-635 Alpaste 51-148B Alpaste 51-231 Alpaste 5205N Alpaste 5207N Alpaste 52-509 Alpaste 52-568 Alpaste 5301N Alpaste 5302N Alpaste 53-119 Alpaste 5422NS Alpaste 54-452 Alpaste 54-497 Alpaste 54-542 Alpaste 55-516 Alpaste 55-519 Alpaste 55-574 Alpaste 5620NS Alpaste 5630NS Alpaste 5640NS Alpaste 56-501 Alpaste 5650NS Alpaste 5653NS Alpaste 5654NS Alpaste 5680N Alpaste 5680NS Alpaste 60-600 Alpaste 60-760 Alpaste 60-768 Alpaste 62-356 Alpaste 6340NS Alpaste 6370NS Alpaste 6390NS Alpaste 640NS Alpaste 65-388 Alpaste 66NLB Alpaste 710N Alpaste 7130N Alpaste 7160N Alpaste 7160NS Alpaste 725N Alpaste 740NS Alpaste 7430NS Alpaste 7580NS Alpaste 7620NS Alpaste 7640NS Alpaste 7670M Alpaste 7670NS Alpaste 7675NS Alpaste 7679NS Alpaste 7680N Alpaste 7680NS Alpaste 76840NS Alpaste 7730N Alpaste 7770N Alpaste 7830N Alpaste 8004 Alpaste 8080N Alpaste 8260NAR Alpaste 891K Alpaste 91-0562 Alpaste 92-0592 Alpaste 93-0595 Alpaste 93-0647 Alpaste 94-2315 Alpaste 95-0570 Alpaste 96-0635 Alpaste 96-2104 Alpaste 97-0510 Alpaste 97-0534 Alpaste AW 520B Alpaste AW 612 Alpaste AW 9800 Alpaste F 795 Alpaste FM 7680K Alpaste FX 440 Alpaste FX 910 Alpaste FZ 0534 Alpaste FZU 40C Alpaste G Alpaste HR 8801 Alpaste HS 2 Alpaste J Alpaste K 9800 Alpaste MC 666 Alpaste MC 707 Alpaste MF 20 Alpaste MG 01 Alpaste MG 1000 Alpaste MG 1300 Alpaste MG 500 Alpaste MG 600 Alpaste MH 6601 Alpaste MH 8801 Alpaste MH 9901 Alpaste MR 7000 Alpaste MR 9000 Alpaste MS 630 Alpaste N 1700NL Alpaste NS 7670 Alpaste O 100N Alpaste O 2130 Alpaste O 300M Alpaste P 0100 Alpaste P 1950 Alpaste S Alpaste SAP 110 Alpaste SAP 414P Alpaste SAP 550N Alpaste SCR 5070 Alpaste TCR 2020 Alpaste TCR 2060 Alpaste TCR 2070 Alpaste TCR 3010 Alpaste TCR 3030 Alpaste TCR 3040 Alpaste TCR 3130 Alpaste TD 200T Alpaste UF 500 Alpaste WB 0230 Alpaste WD 500 Alpaste WJP-U 75C Alpaste WX 0630 Alpaste WX 7830 Alpaste WXA 7640 Alpaste WXM 0630 Alpaste WXM 0650 Alpaste WXM 0660 Alpaste WXM 1415 Alpaste WXM 1440 Alpaste WXM 5422 Alpaste WXM 760b Alpaste WXM 7640 Alpaste WXM 7675 Alpaste WXM-T 60B Alpaste WXM-U 75 Alpaste WXM-U 75C Altop X Aluchrome Ultrafin Super Alumat 1600 Alumet H 30 aluminio Aluminium Aluminium Flake Aluminum 27 Aluminum atom Aluminum element Aluminum Flake PCF 7620 Aluminum granules ALUMINUM METAL/GRANULE ALUMINUM PASTE ALUMINUM PIGMENT ALUMINUM TURNINGS Alumi-paste 640NS Alumipaste 91-0562 Alumipaste 98-1822T Alumipaste AW 620 Alumipaste CR 300 Alumipaste GX 180A Alumipaste GX 201A Alumipaste HR 7000 Alumipaste HR 850 Alumipaste MG 11 Alumipaste MH 8801 Aquamet NPW 2900 Aquapaste 205-5 Aquasilver LPW Astroflake 40 Astroflake Black N 020 Astroflake Black N 070 Astroflake LG 40 Astroflake LG 70 Astroflake Silver N 040 Astroshine NJ 1600 Astroshine T 8990 Atomizalumi VA 200 C.I. PIGMENT METAL 1 Chromal IV Chromal X Decomet 1001/10 Decomet 2018/10 Decomet High Gloss Al 1002/10 Ecka AS 081 Eckart 9155 Eterna Brite 301-1 Eterna Brite 601-1 Eterna Brite 651-1 Eterna Brite EBP 251PA Eterna Brite Primier 251PA Ferro FX 53-038 Friend Color F 500GR-W Friend Color F 500WT Friend Color F 700RE-W Friend Color F 701RE-W Hi Print 60T High Print 60T Hisparkle HS 2 Hydro Paste 8726 Hydrolac WHH 2153 Hydrolan 3560 Hydrolux Reflexal 100 Hydroshine WS 1001 JISA 51010P Kryal Z Lansford 243 LE Sheet 800 Leafing Alpaste LG-H Silver 25 Lunar Al-V 95 Metallux 161 Metallux 2154 Metallux 2192 Metalure Metalure 55350 Metalure L 55350 Metalure L 59510 Metalure W 2001 Metapor Metasheen 1800 Metasheen HR 0800 Metasheen KM 100 Metasheen KM 1000 Metasheen Slurry 1807 Metasheen Slurry 1811 Metasheen Slurry KM 100 Metax G Metax S Mirror Glow 1000 Mirror Glow 600 Mirrorsheen Noral Aluminium Noral Ink Grade Aluminium Obron 10890 Offset FM 4500 Puratronic Reflexal 145 Reynolds 400 Reynolds 4-301 Reynolds 4-591 Reynolds 667 SAP 260PW-HS SAP-FM 4010 SBC 516-20Z Scotchcal 7755SE Serumekku Setanium 50MIS-H8 Siberline ET 2025 Siberline ST 21030E1 Silvar A Silver VT 522 Silverline SSP 353 Silvex 793-20C Sparkle Silver 3141ST Sparkle Silver 3500 Sparkle Silver 3641 Sparkle Silver 5000AR Sparkle Silver 516AR Sparkle Silver 5242AR Sparkle Silver 5245AR Sparkle Silver 5271AR Sparkle Silver 5500 Sparkle Silver 5745 Sparkle Silver 7000AR Sparkle Silver 7005AR Sparkle Silver 7500 Sparkle Silver 960-25E1 Sparkle Silver E 1745AR Sparkle Silver L 1526AR Sparkle Silver Premier 751 Sparkle Silver SS 3130 Sparkle Silver SS 5242AR Sparkle Silver SS 5588 Sparkle Silver SSP 132AR Special PCR 507 Splendal 6001BG Spota Mobil 801 SSP 760-20C Stapa Aloxal PM 2010 Stapa Aloxal PM 3010 Stapa Aloxal PM 4010 Stapa Hydrolac BG 8n.1 Stapa Hydrolac BGH Chromal X Stapa Hydrolac PM Chromal VIII Stapa Hydrolac W 60NL Stapa Hydrolac WH 16 Stapa Hydrolac WH 66NL Stapa Hydrolux 2192 Stapa Hydrolux 8154 Stapa IL Hydrolan 2192-55900G Stapa Metallic R 607 Stapa Metallux 1050 Stapa Metallux 211 Stapa Metallux 212 Stapa Metallux 2196 Stapa Metallux 274 Stapa Mobilux 181 Stapa Offset 3000 Stapa PV 10 Stapa VP 46432G Starbrite 2100 Super Fine 18000 Super Fine 22000 Supramex 2022 Toyo Aluminum 02-0005 Toyo Aluminum 93-3040 Transmet K 102HE Tufflake 3645 Tufflake 5843 UN 1396 US Aluminum 809 Valimet H 2 Valimet H 3 White Silver 7080N White Silver 7130N

DTXSID3040273

15663-27-1

DQLATGHUWYMOKM-UHFFFAOYSA-L

Cisplatin

Cis Platinum, diamminedichloro-, (SP-4-2)- Abiplatin Biocisplatinum Briplatin cis-DDP cis-Diaminedichloroplatinum cis-Diaminedichloroplatinum(II) cis-Diaminodichloroplatinum(II) cis-Diamminedichloroplatinum cis-Diamminedichloroplatinum(II) cis-Dichlorodiamineplatinum(II) cis-Dichlorodiammineplatinum cis-Dichlorodiammineplatinum(II) Cismaplat cis-Platin cisplatine cis-Platine cisplatino cis-Platinous diaminodichloride Cisplatinum cis-Platinum cis-Platinum diaminodichloride cis-Platinum II cis-Platinum(II) diaminodichloride cis-Platinum(II) diamminedichloride cis-Platinumdiamine dichloride cis-Platinumdiammine dichloride Cisplatyl Citoplatino Lederplatin lipoplatin Neoplatin NSC 119875 Platamine Platiblastin Platidiam Platinex Platinol Platinol AQ Platinoxan Platinum, diamminedichloro-, cis- Platistin Platosin SPI 077B103 cis-Dichlorodiamine platinum cis-Dichloro diaminoplatinum II

DTXSID4024983

14797-73-0

VLTRZXGMWDSKGL-UHFFFAOYSA-M

Perchlorate

Perchlorate ion Perchlorate ion (ClO41-) Perchlorate ion(1-) Perchlorate(1-) Perchloric acid, ion(1-)

DTXSID6024252

CHEBI:60311

CHEBI thyroid hormone

UBERON:0002113

UBERON kidney

CHEBI:29101

CHEBI sodium(1+)

CHEBI:16737

CHEBI creatinine

UBERON:0009773

UBERON renal tubule

CHEBI:30660

CHEBI thyroxine

GO:0006590

GO thyroid hormone generation

Q000633

MESH toxicity

GO:0003094

GO glomerular filtration

VT:0005524

VT kidney plasma flow trait

GO:0070293

GO renal absorption

MP:0005332

MP abnormal amino acid level

D004106

MESH Dilatation

MP:0011899

MP podocyte vacuolization

GO:0048102

GO autophagic cell death

MI:0613

MI function

MP:0005475

MP abnormal circulating thyroxine level

WIKI decreased

WIKI occurrence

WIKI increased

Propylthiouracil

2016-11-29T18:42:22

Methimazole

2016-11-29T18:42:19

Manganese

2022-02-04T14:47:23

Chromium

2022-02-03T11:22:01

Gold

2022-02-07T15:25:56

Mercury

2016-11-29T18:42:19

Uranium

2021-08-05T14:28:50

Arsenic

2021-04-27T00:15:21

Zinc

2022-02-04T15:05:00

Aluminum

2022-02-04T14:42:11

Cisplatin

2022-02-03T11:34:57

Perchlorate

2016-11-29T18:42:26

10116

NCBI rat

WCS_9606

common toxicological species human

WCS_8355

common ecological species Xenopus laevis

WCS_7955

common ecological species zebrafish

WCS_90988

common ecological species fathead minnow

9823

NCBI Sus scrofa

WikiUser_15

ApacheUser Sprague-Dawley

10090

NCBI mouse

WCS_9031

common ecological species chicken

9606

NCBI Homo sapiens

Thyroid hormone synthesis, Decreased

TH synthesis, Decreased

Cellular

The thyroid hormones (TH), triiodothyronine (T3) and thyroxine (T4) are thyrosine-based hormones. Synthesis of THs is regulated by thyroid-stimulating hormone (TSH) binding to its receptor and thyroidal availability of iodine via the sodium iodide symporter (NIS). Other proteins contributing to TH production in the thyroid gland, including thyroperoxidase (TPO), dual oxidase enzymes (DUOX), and the transport protein pendrin are also necessary for iodothyronine production (Zoeller et al., 2007). The production of THs in the thyroid gland and resulting serum concentrations are controlled by a negatively regulated feedback mechanism. Decreased T4 and T3 serum concentrations activates the hypothalamus-pituitary-thyroid (HPT) axis which upregulates thyroid-stimulating hormone (TSH) that acts to increase production of additional THs (Zoeller and Tan, 2007). This regulatory system includes: 1) the hypothalamic secretion of the thyrotropin-releasing hormone (TRH); 2) the thyroid-stimulating hormone (TSH) secretion from the anterior pituitary; 3) hormonal transport by the plasma binding proteins; 4) cellular uptake mechanisms at the tissue level; 5) intracellular control of TH concentrations by deiodinating mechanisms; 6) transcriptional function of the nuclear TH receptor; and 7) in the fetus, the transplacental passage of T4 and T3 (Zoeller et al., 2007). TRH and the TSH primarily regulate the production of T4, often considered a “pro-hormone,” and to a lesser extent of T3, the transcriptionally active TH. Most of the hormone released from the thyroid gland into circulation is in the form of T4, while peripheral deiodination of T4 is responsible for the majority of circulating T3. Outer ring deiodination of T4 to T3 is catalyzed by the deiodinases 1 and 2 (DIO1 and DIO2), with DIO1 expressed mainly in liver and kidney, and DIO2 expressed in several tissues including the brain (Bianco et al., 2006). Conversion of T4 to T3 takes place mainly in the liver and kidney, but also in other target organs such as in the brain, the anterior pituitary, brown adipose tissue, thyroid and skeletal muscle (Gereben et al., 2008; Larsen, 2009).  In mammals, most evidence for the ontogeny of TH synthesis comes from measurements of serum hormone concentrations. And, importantly, the impact of xenobiotics on fetal hormones must include the influence of the maternal compartment since a majority of fetal THs are derived from maternal blood early in fetal life, with a transition during mid-late gestation to fetal production of THs that is still supplemented by maternal THs. In humans, THs can be found in the fetus as early as gestational weeks 10-12, and concentations rise continuously until birth. At term, fetal T4 is similar to maternal levels, but T3 remains 2-3 fold lower than maternal levels. In rats, THs can be detected in the fetus as early as the second gestational week, but fetal synthesis does not start until gestational day 17 with birth at gestational day 22-23. Maternal THs continue to supplement fetal production until parturition. (see Howdeshell, 2002; Santisteban and Bernal, 2005 for review). Due to the maternal factor, the life stage specific impact of TPO inhibition after exposure to environmental chemicals is complex (Ramhoj et al., 2022). Decreased TH synthesis in the thyroid gland may result from several possible molecular-initiating events (MIEs) including: 1) Disruption of key catalytic enzymes or cofactors needed for TH synthesis, including TPO, NIS, or dietary iodine insufficiency. Theoretically, decreased synthesis of Tg could also affect TH production (Kessler et al., 2008; Yi et al., 1997). Mutations in genes that encode requisite proteins in the thyroid may also lead to impaired TH synthesis, including mutations in pendrin associated with Pendred Syndrome (Dossena et al., 2011), mutations in TPO and Tg (Huang and Jap 2015), and mutations in NIS (Spitzweg and Morris, 2010). 2) Decreased TH synthesis in cases of clinical hypothyroidism may be due to Hashimoto's thyroiditis or other forms of thyroiditis, or physical destruction of the thyroid gland as in radioablation or surgical treatment of thyroid lymphoma. 3) It is possible that TH synthesis may also be reduced subsequent to disruption of the negative feedback mechanism governing TH homeostasis, e.g. pituitary gland dysfunction may result in a decreased TSH signal with concomitant T3 and T4 decreases. 4) More rarely, hypothalamic dysfunction can result in decreased TH synthesis.  Increased fetal TH levels are also possible. Maternal Graves disease, which results in fetal thyrotoxicosis (hyperthyroidism and increased serum T4 levels), has been successfully treated by maternal administration of TPO inhibitors (c.f., Sato et al., 2014).   It should be noted that different species and different life stages store different amounts of TH precursors and iodine within the thyroid gland. Thus, decreased TH synthesis via transient iodine insufficiency or inhibition of TPO may not affect TH release from the thyroid gland until depletion of stored iodinated Tg. Adult humans may store sufficient Tg-DIT residues to serve for several months to a year of TH demand (Greer et al., 2002; Zoeller, 2004). Neonates and infants have a much more limited supply of less than a week. While the TH system is highly conserved across vertebrates, there are some taxon-specific considerations. Zebrafish and fathead minnows are oviparous fish species in which maternal THs are transferred to the eggs and regulate early embryonic developmental processes during external (versus intra-uterine in mammals) development (Power et al., 2001; Campinho et al., 2014; Ruuskanen and Hsu, 2018) until embryonic TH synthesis is initiated. Maternal transfer of THs to the eggs has been demonstrated in zebrafish (Walpita et al., 2007; Chang et al., 2012) and fathead minnows (Crane et al., 2004; Nelson et al., 2016). Decreases in TH synthesis can only occur after initiation of embryonic TH synthesis. The components of the TH system responsible for TH synthesis are highly conserved across vertebrates and therefore interference with the same molecular targets compared to mammals can lead to decreased TH synthesis (TPO, NIS, etc.) in fish. Endogenous transcription profiles of thyroid-related genes in zebrafish and fathead minnow showed that mRNA coding for these genes is also maternally transferred and increasing expression of most transcripts during hatching and embryo-larval transition indicates a fully functional HPT axis in larvae (Vergauwen et al., 2018). Although the HPT axis is highly conserved, there are some differences between fish and mammals (Blanton and Specker, 2007; Deal and Volkoff, 2020). For example, in fish, corticotropin releasing hormone (CRH) often plays a more important role in regulating thyrotropin (TSH) secretion by the pituitary and thus TH synthesis compared to TSH-releasing hormone (TRH). Also, in most fish species thyroid follicles are more diffusely located in the pharyngeal region rather than encapsulated in a gland.

Decreased TH synthesis is often implied by measurement of TPO and NIS inhibition measured clinically and in laboratory models as these enzymes are essential for TH synthesis. Rarely is decreased TH synthesis measured directly, but rather the impact of chemicals on the quantity of T4 produced in the thyroid gland, or the amount of T4 present in serum is used as a marker of decreased T4 release from the thyroid gland (e.g., Romaldini et al., 1988). Methods used to assess TH synthesis include, incorporation of radiolabeled tracer compounds, radioimmunoassay, ELISA, and analytical detection.    Recently, amphibian thyroid explant cultures have been used to demonstrate direct effects of chemicals on TH synthesis, as this model contains all necessary synthesis enzymes including TPO and NIS (Hornung et al., 2010). For this work THs was measured by HPLC/ICP-mass spectometry. Decreased TH synthesis and release, using T4 release as the endpoint, has been shown for thiouracil antihyperthyroidism drugs including MMI, PTU, and the NIS inhibitor perchlorate (Hornung et al., 2010). Techniques for in vivo analysis of TH system disruption among other drug-related effects in fish were reviewed by Raldua and Piña (2014). TIQDT (Thyroxine-immunofluorescence quantitative disruption test) is a method that provides an immunofluorescent based estimate of thyroxine in the gland of zebrafish (Raldua and Babin, 2009; Thienpont et al., 2011; Jomaa et al., 2014; Rehberger et al., 2018).  Thienpont used this method with ~25 xenobiotics (e.g., amitrole, perchlorate, methimazole, PTU, DDT, PCBs). The method detected changes for all chemicals known to directly impact TH synthesis in the thyroid gland (e.g., NIS and TPO inhibitors), but not those that upregulate hepatic catabolism of T4. Rehberger et al. (2018) updated the method to enable simultaneous semi-quantitative visualization of intrafollicular T3 and T4 levels. Most often, whole body TH level measurements in fish early life stages are used as indirect evidence of decreased TH synthesis (Nelson et al., 2016; Stinckens et al., 2016; Stinckens et al., 2020). Analytical determination of TH levels by LC-MS is becoming increasingly available (Hornung et al., 2015). More recently, transgenic zebrafish with fluorescent thyroid follicles are being used to visualize the compensatory proliferation of the thyroid follicles following inhibition of TH synthesis among others (Opitz et al., 2012).

Taxonomic: This KE is plausibly applicable across vertebrates. Decreased TH synthesis resulting from TPO or NIS inhibition is conserved across vertebrate taxa, with in vivo evidence from humans, rats, amphibians, some fish species, and birds, and in vitro evidence from rat and porcine microsomes. Indeed, TPO and NIS mutations result in congenital hypothyroidism in humans (Bakker et al., 2000; Spitzweg and Morris, 2010), demonstrating the essentiality of TPO and NIS function toward maintaining euthyroid status. Though decreased serum T4 is used as a surrogate measure to indicate chemical-mediated decreases in TH synthesis, clinical and veterinary management of hyperthyroidism and Graves’ disease using propylthiouracil and methimazole, known to decrease TH synthesis, indicates strong evidence for chemical inhibition of TPO (Zoeller and Crofton, 2005). Life stage: Applicability to certain life stages may depend on the species and their dependence on maternally transferred THs during the earliest phases of development. The earliest life stages of teleost fish (e.g., fathead minnow, zebrafish) rely on maternally transferred THs to regulate certain developmental processes until embryonic TH synthesis is active (Power et al., 2001). In externally developing fish species, decreases in TH synthesis can only occur after initiation of embryonic TH synthesis. In zebrafish, Opitz et al. (2011) showed the formation of a first thyroid follicle at 55 hours post fertilization (hpf), Chang et al. (2012) showed a first significant TH increase at 120 hpf and Walter et al. (2019) showed clear TH production already at 72 hpf but did not analyse time points between 24 and 72 hpf. TPO inhibition in a homozygous knockout line abolished the T4 production in thyroid follicles of mutant zebrafish with phenotypic abnormalities occurring from 20 dpf onwards but not before 10 dpf (Fang et al., 2022). Therefore, it is still uncertain when exactly embryonic TH synthesis is activated and thus when exactly this process becomes sensitive to disruption. In fathead minnows, a significant increase of whole body TH levels was already observed between 1 and 2 dpf, which corresponds to the appearance of the thyroid anlage at 35 hpf prior to the first observation of thyroid follicles at 58 hpf (Wabuke-Bunoti and Firling, 1983). It currently remains unclear when exactly embryonic TH production is initiated in zebrafish. Sex: The KE is plausibly applicable to both sexes. THs are essential in both sexes and the components of the HPT-axis are identical in both sexes. There can however be sex-dependent differences in the sensitivity to the disruption of TH levels and the magnitude of the response. In humans, females appear more susceptible to hypothyroidism compared to males when exposed to certain halogenated chemicals (Hernandez‐Mariano et al., 2017; Webster et al., 2014). In adult zebrafish, Liu et al. (2019) showed sex-dependent changes in TH levels and mRNA expression of regulatory genes including corticotropin releasing hormone (crh), thyroid stimulating hormone (tsh) and deiodinase 2 after exposure to organophosphate flame retardants. The underlying mechanism of any sex-related differences remains unclear.

UBERON:0002046

UBERON thyroid gland

CL:0002258

CL thyroid follicular cell

High Male High Female

High

All life stages

High High Moderate High Moderate High

Bakker B, Bikker H, Vulsma T, de Randamie JS, Wiedijk BM, De Vijlder JJ. 2000. Two decades of screening for congenital hypothyroidism in The Netherlands: TPO gene mutations in total iodide organification defects (an update). The Journal of clinical endocrinology and metabolism.  85:3708-3712. Bianco AC, Kim BW. (2006). Deiodinases: implications of the local control of thyroid hormone action. J Clin Invest. 116: 2571–2579. Blanton ML, Specker JL. 2007. The hypothalamic-pituitary-thyroid (hpt) axis in fish and its role in fish development and reproduction. Crit Rev Toxicol. 37(1-2):97-115. Campinho MA, Saraiva J, Florindo C, Power DM. 2014. Maternal thyroid hormones are essential for neural development in zebrafish. Molecular Endocrinology. 28(7):1136-1149. Chang J, Wang M, Gui W, Zhao Y, Yu L, Zhu G. 2012. Changes in thyroid hormone levels during zebrafish development. Zoological Science. 29(3):181-184. Crane HM, Pickford DB, Hutchinson TH, Brown JA. 2004. Developmental changes of thyroid hormones in the fathead minnow, pimephales promelas. General and Comparative Endocrinology. 139(1):55-60. Deal CK, Volkoff H. 2020. The role of the thyroid axis in fish. Frontiers in Endocrinology. 11. Dossena S, Nofziger C, Brownstein Z, Kanaan M, Avraham KB, Paulmichl M. (2011). Functional characterization of pendrin mutations found in the Israeli and Palestinian populations. Cell Physiol Biochem. 28: 477-484.Gereben B, Zavacki AM, Ribich S, Kim BW, Huang SA, Simonides WS, Zeöld A, Bianco AC. (2008). Cellular and molecular basis of deiodinase-regulated thyroid hormone signalling. Endocr Rev. 29:898–938. Fang, Y., Wan, J. P., Zhang, R. J., Sun, F., Yang, L., Zhao, S. X., Dong, M., & Song, H. D. (2022). Tpo knockout in zebrafish partially recapitulates clinical manifestations of congenital hypothyroidism and reveals the involvement of TH in proper development of glucose homeostasis. General and Comparative Endocrinology, 323–324. https://doi.org/10.1016/j.ygcen.2022.114033 Gereben B, Zeöld A, Dentice M, Salvatore D, Bianco AC.  Activation and inactivation of thyroid hormone by deiodinases: local action with general consequences.  Cell Mol Life Sci. 2008 Feb;65(4):570-90 Greer MA, Goodman G, Pleus RC, Greer SE. Health effects assessment for environmental perchlorate contamination: the dose response for inhibition of thyroidal radioiodine uptake in humans. Environ Health Perspect. 2002. 110:927-937. Hernandez-Mariano JA, Torres-Sanchez L, Bassol-Mayagoitia S, Escamilla-Nunez M, Cebrian ME, Villeda-Gutierrez EA, Lopez-Rodriguez G, Felix-Arellano EE, Blanco-Munoz J. 2017. Effect of exposure to p,p '-dde during the first half of pregnancy in the maternal thyroid profile of female residents in a mexican floriculture area. Environmental Research. 156:597-604. Hornung MW, Degitz SJ, Korte LM, Olson JM, Kosian PA, Linnum AL, Tietge JE. 2010. Inhibition of thyroid hormone release from cultured amphibian thyroid glands by methimazole, 6-propylthiouracil, and perchlorate. Toxicol Sci 118:42-51. Hornung MW, Kosian PA, Haselman JT, Korte JJ, Challis K, Macherla C, Nevalainen E, Degitz SJ. 2015. In vitro, ex vivo, and in vivo determination of thyroid hormone modulating activity of benzothiazoles. Toxicological Sciences. 146(2):254-264. Howdeshell KL. 2002. A model of the development of the brain as a construct of the thyroid system. Environ Health Perspect. 110 Suppl 3:337-48. Huang CJ and Jap TS. 2015. A systematic review of genetic studies of thyroid disorders in Taiwan. J Chin Med Assoc. 78: 145-153. Jomaa B, Hermsen SAB, Kessels MY, van den Berg JHJ, Peijnenburg AACM, Aarts JMMJG, Piersma AH, Rietjens IMCM. 2014. Developmental toxicity of thyroid-active compounds in a zebrafish embryotoxicity test. Altex-Alternatives to Animal Experimentation. 31(3):303-317. Kessler J, Obinger C, Eales G. Factors influencing the study of peroxidase-generated iodine species and implications for thyroglobulin synthesis. Thyroid. 2008 Jul;18(7):769-74. doi: 10.1089/thy.2007.0310 Larsen PR. (2009). Type 2 iodothyronine deiodinase in human skeletal muscle: new insights into its physiological role and regulation. J Clin Endocrinol Metab. 94:1893-1895. Liu XS, Cai Y, Wang Y, Xu SH, Ji K, Choi K. 2019. Effects of tris(1,3-dichloro-2-propyl) phosphate (tdcpp) and triphenyl phosphate (tpp) on sex-dependent alterations of thyroid hormones in adult zebrafish. Ecotoxicology and Environmental Safety. 170:25-32. Nelson K, Schroeder A, Ankley G, Blackwell B, Blanksma C, Degitz S, Flynn K, Jensen K, Johnson R, Kahl M et al. 2016. Impaired anterior swim bladder inflation following exposure to the thyroid peroxidase inhibitor 2-mercaptobenzothiazole part i: Fathead minnow. Aquatic Toxicology. 173:192-203. Opitz R, Maquet E, Huisken J, Antonica F, Trubiroha A, Pottier G, Janssens V, Costagliola S. 2012. Transgenic zebrafish illuminate the dynamics of thyroid morphogenesis and its relationship to cardiovascular development. Developmental Biology. 372(2):203-216. Opitz R, Maquet E, Zoenen M, Dadhich R, Costagliola S. 2011. Tsh receptor function is required for normal thyroid differentiation in zebrafish. Molecular Endocrinology. 25(9):1579-1599. Power DM, Llewellyn L, Faustino M, Nowell MA, Bjornsson BT, Einarsdottir IE, Canario AV, Sweeney GE. 2001. Thyroid hormones in growth and development of fish. Comp Biochem Physiol C Toxicol Pharmacol. 130(4):447-459. Raldua D, Babin PJ. 2009. Simple, rapid zebrafish larva bioassay for assessing the potential of chemical pollutants and drugs to disrupt thyroid gland function. Environmental Science & Technology. 43(17):6844-6850. Raldua D, Pina B. 2014. In vivo zebrafish assays for analyzing drug toxicity. Expert Opinion on Drug Metabolism & Toxicology. 10(5):685-697. Ramhoj, L., Svingen, T., Fradrich, C., Rijntjes, E., Wirth, E.K., Pedersen, K., Kohrle, J., Axelstad, M., 2022. Perinatal exposure to the thyroperoxidase inhibitors methimazole and amitrole perturbs thyroid hormone system signaling and alters motor activity in rat offspring. Toxicology Letters 354, 44-55. Rehberger K, Baumann L, Hecker M, Braunbeck T. 2018. Intrafollicular thyroid hormone staining in whole-mount zebrafish (danio rerio) embryos for the detection of thyroid hormone synthesis disruption. Fish Physiology and Biochemistry. 44(3):997-1010. Romaldini JH, Farah CS, Werner RS, Dall'Antonia Júnior RP, Camargo RS. 1988.  "In vitro" study on release of cyclic AMP and thyroid hormone in autonomously functioning thyroid nodules.  Horm Metab Res.20:510-2. Ruuskanen S, Hsu BY. 2018. Maternal thyroid hormones: An unexplored mechanism underlying maternal effects in an ecological framework. Physiological and Biochemical Zoology. 91(3):904-916. Santisteban P, Bernal J. Thyroid development and effect on the nervous system. Rev Endocr Metab Disord. 2005 Aug;6(3):217-28. Spitzweg C, Morris JC. 2010. Genetics and phenomics of hypothyroidism and goiter due to NIS mutations. Molecular and cellular endocrinology. 322:56-63. Stinckens E, Vergauwen L, Blackwell BR, Anldey GT, Villeneuve DL, Knapen D. 2020. Effect of thyroperoxidase and deiodinase inhibition on anterior swim bladder inflation in the zebrafish. Environmental Science & Technology. 54(10):6213-6223. Stinckens E, Vergauwen L, Schroeder A, Maho W, Blackwell B, Witters H, Blust R, Ankley G, Covaci A, Villeneuve D et al. 2016. Impaired anterior swim bladder inflation following exposure to the thyroid peroxidase inhibitor 2-mercaptobenzothiazole part ii: Zebrafish. Aquatic Toxicology. 173:204-217. Thienpont B, Tingaud-Sequeira A, Prats E, Barata C, Babin PJ, Raldúa D.  Zebrafish eleutheroembryos provide a suitable vertebrate model for screening chemicals that impair thyroid hormone synthesis.  Environ Sci Technol. 2011. 45(17):7525-32. Vergauwen L, Cavallin JE, Ankley GT, Bars C, Gabriels IJ, Michiels EDG, Fitzpatrick KR, Periz-Stanacev J, Randolph EC, Robinson SL et al. 2018. Gene transcription ontogeny of hypothalamic-pituitary-thyroid axis development in early-life stage fathead minnow and zebrafish. General and Comparative Endocrinology. 266:87-100. Wabukebunoti MAN, Firling CE. 1983. The prehatching development of the thyroid-gland of the fathead minnow, pimephales-promelas (rafinesque). General and Comparative Endocrinology. 49(2):320-331. Walpita CN, Van der Geyten S, Rurangwa E, Darras VM. 2007. The effect of 3,5,3'-triiodothyronine supplementation on zebrafish (danio rerio) embryonic development and expression of iodothyronine deiodinases and thyroid hormone receptors. Gen Comp Endocrinol. 152(2-3):206-214. Walter KM, Miller GW, Chen XP, Yaghoobi B, Puschner B, Lein PJ. 2019. Effects of thyroid hormone disruption on the ontogenetic expression of thyroid hormone signaling genes in developing zebrafish (danio rerio). General and Comparative Endocrinology. 272:20-32. Webster GM, Venners SA, Mattman A, Martin JW. 2014. Associations between perfluoroalkyl acids (pfass) and maternal thyroid hormones in early pregnancy: A population-based cohort study. Environmental Research. 133:338-347. Yi X, Yamamoto K, Shu L, Katoh R, Kawaoi A. Effects of Propyithiouracil (PTU) Administration on the Synthesis and Secretion of Thyroglobulin in the Rat Thyroid Gland: A Quantitative Immuno-electron Microscopic Study Using Immunogold Technique. Endocr Pathol. 1997 Winter;8(4):315-325. Zoeller RT, Crofton KM. 2005.  Mode of action: developmental thyroid hormone insufficiency--neurological abnormalities resulting from exposure to propylthiouracil. Crit Rev Toxicol. 35:771-81 Zoeller RT, Tan SW, Tyl RW. 2007. General background on the hypothalamic-pituitary-thyroid (HPT) axis. Critical reviews in toxicology.  37:11-53. Zoeller RT.  Interspecies differences in susceptibility to perturbation of thyroid hormone homeostasis requires a definition of "sensitivity" that is informative for risk analysis. Regul Toxicol Pharmacol. 2004 Dec;40(3):380.   AOPWiki 2016-11-29T18:41:23

2022-11-04T09:25:39

Occurrence, Kidney toxicity

Organ

The kidneys are a crucial site of regulation of divalent cation levels in the plasma through filtration, reabsorption, and concentration (cite). On top of their excretion capabilities, the kidneys are also responsible for the production of hormones crucial for hematologic, cardiovascular, and skeletal muscle homeostasis (Bonventre et al., 2010). Nephrons are the functional units of the kidney and each kidney is made up of approximately 1 million nephrons (Bonventre et al., 2010). The nephrons are vital in reabsorption of these cations where 70% of transport has been shown to occur in the proximal tubule (Barbier et al., 2005). The kidneys are thought to be very susceptible to toxicity due to the increased concentration through their filtering structures with the tubular uptake mechanisms, specifically those of the proximal tubule, magnifying intracellular concentrations (Bonventre et al., 2010; Weber et al., 2017). Commonly, biomarkers like serum creatinine (sCr) and blood urea nitrogen (BUN) are utilized to identify kidney toxicity; however, these markers have been identified as nonspecific to the area of the kidney and slow in identification. Bonventre et al. (2010) has explored other biomarkers that may be used to identify segment specific injury. Proximal tubule injury can be identified using: albumin, RPB, NAG, clusterin, osteopontin, a1-microglobulin, and many others. Glomerulus damage can be identified through urinary Cystatin C, b2-microglobulin, a1-microglobulin, albumin, and more (Bonventre et al., 2010). These biomarkers do show some overlap between regions and can indicate damage to various areas of the nephron, though it is important to note the development of these specific techniques and therefore, the ability to develop more tailored and earlier identifying testing procedures. Since there are many essential metals for cellular function, there are also many transporters responsible for facilitating ionic entry into the cell and the designated cellular compartment (cite). Some of these transporters are very specific to a given metal and some are more diverse in the metals they handle, therefore, these transporters can facilitate the transport of toxic metals into the cell, often through mimickery exhibited by those metals (Ballatori, 2002). DMT1 (divalent metal transporter 1) is a strong example of such transporters. The introduction of toxic divalent cations (Cd2+, Pb2+, Pt2+, etc.) is highly problematic in the kidneys due to increased toxicity and occupancy of DMT1 limiting the transport of essential trace elements. DMT1 is an essential transport molecule that is highly expressed in the kidneys, and is responsible for transport of essential trace divalent cations, as well as highly toxic ones; this competition increases strain on the kidneys exposed to toxic heavy metals (Barbier et al., 2005; Ballatori, 2002). DMT1 has been shown to transport Fe, Zn, Mn, Co, Cd, Cu, Ni, and Pb via a proton-coupled, membrane potential dependant mechanism (Ballatori, 2002). Some toxic metals can also enter a cell by forming complexes that mimic endogenous molecules in their structure. Arsenate and vanadate, for example, act as phosphate mimics both for transport and metabolism, assaulting cellular function by the same mechanism as their initial entry; cromate, selenite and molybdate mimic sulfate in a similar way (Ballatori, 2002). Many of the identified transporters fooled by this mimicry have been localized to the brush border membrane of the renal proximal tubule and epithelial cells. Some divalent metals such as Cd, Ba, and Sr have been shown to enter cells through voltage gated calcium channels. Another important example focused on by Ballatori (2002) is the action of inorganic mercury and methyl mercury (MeHg) that were shown to have high affinity for reduced sulfhydryl groups. These groups are seen on the amino acid cysteine, and importantly on glutathione (GSH), a vital enzymatic antioxidant. MeHg mimics methionine to enter the cell, after which it binds to GSH, and interferes with ATP production (Ballatori, 2002). Uranium has been shown to enter the blood rapidly and then either form stable complexes with plasma proteins, due to its high affinity for phosphate, carboxyl and hydroxyl groups, or binds to bicarbonate in the blood (Keith et al., 2013). In the kidneys, uranium can be released from bicarbonate to combine with other small proteins in the kidney tubular walls, disrupting cellular function (Keith et al., 2013). Uranium has been seen to enter the glomerulus, where it is filtered, via endocytosis as UO+2 binding to anionic sites of proximal tubular epithelial brush borders (Shaki et al., 2012). To further understand the mode of action of heavy metals within the kidneys, many studies have been conducted to determine the specific region primarily damaged. It is also important to note that variation of results may be found in some studies as experimental conditions as well as other factors may influence the mode of action of some metals. Zamora et al. (1998) found that kidney function decrease and cytotoxicity increase were correlated with uranium ingestion. However, no glomerular injury was detected, indicating that chronic uranium ingestion in rats (0.004 µg/kg to 9 µg/kg body weight) damages the proximal tubule and not the glomerulus (Zamora et al., 1998). Homma-Takeda et al. (2013) identifies the kidneys as the major site of depleted uranium toxicity. Studying the kidneys of rats of varying ages, exposed to 0.1-2mg/kg uranyl acetate, they found that the younger kidneys did not flush the uranium out as well. Accumulation of uranium and its damages was seen in the S3 segment of the proximal tubules (Homma-Takeda et al., 2013). Shaki et al. (2012), assessed the mechanism of depleted uranium-induced nephrotoxicity that revealed damage to the mitochondria isolated from uranyl acetate treated rat kidney cells. The damage included oxidative stress, mitochondrial swelling, mitochondrial membrane potential collapse, cytochrome C release, impaired ATP production, and damage to the electron transport chain complexes. Utilizing rat renal brush border vesicles, Goldman et al. (2006) found that exposure to uranyl acetate induced decreased rates of glucose transport, in part due to a decreased number of sodium-coupled glucose transporters; this decreased the ability of the kidneys to reabsorb glucose properly. Berradi et al. (2008) assessed the red blood cell (RBC) count of rats drinking water containing 40mg DU/L and found that chronic exposure to DU causes RBC reduction, pointing to nephrotoxicity as the kidneys play a major role in RBC synthesis. Heavy metals consistently aggregate in the kidneys, and more specifically in the S3 segment of the proximal tubules. Evidence also suggests that uranium and other heavy metals induce nephrotoxicity after endocytosis into cells by disrupting the electron transport chain, inducing oxidative stress. The oxidative stress leads to mitochondrial dysfunction followed by, apoptosis at low doses of uranium and necrosis at  high doses of uranium. Finally, this induces renal injury and tissue damage to the proximal tubules, or nephrotoxicity.

<table border="1" cellpadding="1" cellspacing="1" style="width:500px"> <tbody> <tr> <td>Assay Type & Measured Content</td> <td> Description </td> <td>Dose Range Studied</td> <td> Assay Characteristics (Length/Ease of use/Accuracy) </td> </tr> <tr> <td> Kidney Function Assay Measuring total urinary protein, albumin, transferrin, b2-microglobulin, retinolbinding protein, brush border tubular antigens, N-acetyl-b-Dglucosaminidase activity, serum and urinary creatine (de Burbure et al., 2003) </td> <td>“All analyses of a given parameter were performed under similar experimental conditions in the same laboratories within 6mo of collection. Total urinary protein (Prot-T-U) was determined by the Coomassie blue G250 binding method. Albumin (Alb-U), transferrin (Transf-U), β2-microglobulin (β2m-U), and retinolbinding protein (RBP-U) in urine were quantified by latex immunoassay (Bernard & Lauwerys, 1983). Acceptable limits for precision and accuracy of measurements and external quality controls were the same as those described in the Cadmibel study (Lauwerys et al., 1990). The brush border tubular antigens (BBA-U) were analyzed by a sandwich enzyme-linked immunoassay using monoclonal antibodies (Mutti et al., 1985). The total activity of N-acetyl-β-Dglucosaminidase (NAG-T-U) in urine was determined colorimetrically using a kit (PPR Diagnostics Ltd.) as described elsewhere (Price et al., 1996). Only total NAG (NAG-T) was used for the purpose of this study. Serum and urinary creatinine (Creat-U) were measured by the methods of Heinegard and Tiderström (1973), and Jaffé, respectively (Henry, 1965).” (de Burbure et al., 2003)</td> <td>“The soil contamination in the area varied from 100 to 1700ppm lead (with values higher than 1000ppm in the immediate vicinity of the factories), 0.7 to 233ppm cadmium, and 101 to 22,257ppm zinc, with the highest concentrations being recorded within 500 m of the 2 factories”</td> <td> </td> </tr> <tr> <td> NAG Assay Measuring N-acetyl-b-D-Glucosaminidase urinary content (Lim et al., 2016)</td> <td>“Urinary NAG activity was measured by using NAG Quantitative Kit (Shionogi, Osaka, Japan). After storing a synthetic substrate solution (1 mL) at 37°C for five minutes, the solution was mixed with the supernatant of the urine samples (50 mL) received after centrifugation. After storing it at 37°C for 15 min, stopping solution (2 mL) was added to and mixed with it. By using a spectrophotometer, its fluorescence intensities were measured with a wavelength of 580 nm (<a href="https://www.ncbi.nlm.nih.gov/pmc/articles/PMC4780232/#b13-tr-32-057" style="color:#0563c1; text-decoration:underline">13</a>,<a href="https://www.ncbi.nlm.nih.gov/pmc/articles/PMC4780232/#b14-tr-32-057" style="color:#0563c1; text-decoration:underline">14</a>). Urinary β2-MG was measured by using Enzygnost β2-MG Micro Kit (Behring Institute, Mannheim, Germany). Its method used the principle of solid phase enzyme-linked immunosorbent assay (ELISA). Monoclonal anti-β2-MG antibody and anti-2-MG-horseradish peroxidase conjugate solution were used. After that, color intensities were measured with a wavelength of 450 nm by using a spectrophotometer (<a href="https://www.ncbi.nlm.nih.gov/pmc/articles/PMC4780232/#b13-tr-32-057" style="color:#0563c1; text-decoration:underline">13</a>,<a href="https://www.ncbi.nlm.nih.gov/pmc/articles/PMC4780232/#b14-tr-32-057" style="color:#0563c1; text-decoration:underline">14</a>).” (Lim et al., 2016)</td> <td> Pb: 0.0221ppm (converted from blood Pb µg/dL) Cd: 1.08ppm (converted from Urinary Cd μg/g creatinine)</td> <td>Fast, easy, accurate</td> </tr> <tr> <td> Kidney Dysfunction Assay Measuring BUN and creatinine serum blood levels (Shaki et al., 2012)</td> <td>“For studies in vivo rats were fasted overnight, then animals were divided into two groups, with six rats in each group. The control group (vehicle) received a single intraperitoneal (i.p.) injection of saline solution (1 ml per 100 g body weight). Uranyl acetate was dissolved in normal saline. Rats were treated with single intraperitoneal (i.p.) injections of UA in doses 0.5, 1 and 2 mg/kg body weight. These dosages was selected based on previous studies [28], which is sufficient to induce oxidative stress in kidney without causing death and none died within the duration of experiments. Blood urea nitrogen (BUN) and creatinine, marker of kidney dysfunction, were determined by commercial reagents (obtained from Parsazmoon Co., Iran). The rats were killed by decapitation 24 h after injection. The kidney were immediately removed and placed in ice-cold mitochondria isolation medium (0.225 M D-mannitol, 75 mM sucrose, and 0.2 mM EDTA, pH=7.4)” (Shaki et al., 2012)</td> <td>Control, 0.5, 1, 2 mg/kg Uranyl Acetate (UA) </td> <td>Fast, easy, medium accuracy </td> </tr> </tbody> </table>

Higher order animals (mammals) with functional and complete kidneys

UBERON:0002113

UBERON kidney

Not Specified Not Specified

Al Dera, H. S. (2016). Protective effect of resveratrol against aluminum chloride induced nephrotoxicity in rats. Saudi Med J, 37(4), 369-378. doi:10.15537/smj.2016.4.13611 Andjelkovic, M., Djordjevic, A. B., Antonijevic, E., Antonijevic, B., Stanic, M., Kotur-Stevuljevic, J., . . . Bulat, Z. (2019). Toxic effect of acute cadmium and lead exposure in rat blood, liver, and kidney. International Journal of Environmental Research and Public Health, 16, 247. doi:10.3390/ijerph16020274 Arzuaga , X., Rieth, S. H., Bathija, A. & Cooper, G. S. (2010) Renal Effects of Exposure to Natural and Depleted Uranium: A Review of the Epidemiologic and Experimental Data, Journal of Toxicology and Environmental Health, Part B, 13:7-8, 527-545, DOI:10.1080/10937404.2010.509015 Ballatori, N. (2002). Transport of toxic metals by molecular mimicry. Environmental Health Perspectives, 110, 689-694. doi:10.1289/ehp.02110s5689 Barnes, P., Yeboah, J. K., Gbedema, W., Saahene, R. O., & Amoani, B. (2020). Ameliorative effect of vernonia amygdalina plant extract on heavy metal-induced LIver and kidney dysfunction in rats. Advances in Pharmacological and Pharmaceutical Sciences, 2020, 1-7. doi:10.1155/2020/2976905 Barbier, O., Jcquillet, G., Tauc, M., Cougnon, M., & Poujeol, P. (2005). Effect of heavy metals on, and handling by, the  kidney. Nephron Physiology, 99, 105-110. doi:10.1159/000083981 Bonventre, J. V., Vaidya, V. S., Schmouder, R., Feig, P., & Dieterle, F. (2010). Next-generation biomarkers for detecting kidney toxicity. Nature biotechnology, 28(5), 436–440. <a href="https://doi.org/10.1038/nbt0510-436" style="color:#0563c1; text-decoration:underline">https://doi.org/10.1038/nbt0510-436</a> Brzoska, M. M., Kaminski, M., Supernak-Bobko, D., Zwierz, K., & Moniuszko-Jakoniuk, J. (2003). Changes in the strucutre and function of the kidney of rats chronically exposed to cadmium. I. biochemical and histopathological studies. Arch.Toxicol., 77, 344-352. doi:10.1007/s00204-003-0451-1 Buelna-Chontal, M., Franco, M., Hernandez-Esquivel, L., Pavon, N., Rodriguez-Zalvala, J. S., Correa, F., . . . Chavez, E. (2017). CDP-choline circumvents mercury-induced mitochondrial damage and renal dysfunction. Cell Biology International, 41, 1356-1366. doi:10.1002/cbin.10871 Chtourou, Y., Garoui, E. m., Boudawara, T., & Zeghal, N. (2014). Protective role of silymarin against manganese-induced nephrotoxicity and oxidative stress in rat. Environ Toxicol, 29, 1147-1154. doi:10.1002/tox.21845 Durante, P., Romero, F., Perez, M., Chavez, M., & Parra, G. (2010). Effect of uric acid on nephrotoxicity induced by mercuric chloride in rats. Toxicology and Industrial Health, 26(3), 163-174. doi:10.1177/0748233710362377 García-Niño, W. R., Tapia, E., Zazueta, C., Zatarain-Barrón, Z. L., Hernández-Pando, R., Vega-García, C. C., & Pedraza-Chaverrí, J. (2013). Curcumin pretreatment prevents potassium dichromate-induced hepatotoxicity, oxidative stress, decreased respiratory complex I activity, and membrane permeability transition pore opening. Evidence-Based Complementary and Alternative Medicine, (424692), 1-19. doi:10.1155/2013/424692 Goldman, M., Yaari, A., Doshnitzki, Z., Cohen-Luria, R., & Moran, A. (2006). Nephrotoxicity of uranyl acetate: Effect on rat kidney brush border membrane vesicles. Archives of Toxicology, 80(7), 387-393. doi:10.1007/s00204-006-0064-6 Homma-Takeda S, Kokubo T, Terada Y, Suzuki K, Ueno S, Hayao T, Inoue T, Kitahara K, Blyth BJ, Nishimura M, Shimada Y. Uranium dynamics and developmental sensitivity in rat kidney. J Appl Toxicol. 2013 Jul;33(7):685-94. doi: 10.1002/jat.2870. Epub 2013 Apr 26. PMID: 23619997. Keith, S., Faroon, O., N., R., Scinicariello, F., Wilbur, S., Ingerman, L., . . . Diamond, G. (2013). Toxicological profile for uranium. U.S. Department of Health and Human Services. Agency for Toxic Substances and Disease Registry. Kharroubi, W., Dhibi, M., Mekni, M., Haouas, Z., Chreif, I., Neffati, F., . . . Sakly, R. (2014). Sodium arsenate induce changes in fatty acids profiles and oxidative damage in kidney of rats. Environ Sci Pollut Res, 21, 12040-12049. doi:10.1007/s11356-014-3142-y Lunyera, J., & Smith, S. R. (2017). Heavy metal nephropathy: Considerations for exposure analysis. Kidney International, 92, 548-550. doi:http://dx.doi.org/10.1016/j.kint.2017.04.043 Sabath, E., & Robles-Osorio, M. L. (2012). Renal health and the environment: Heavy metal nephrotoxicity. Revista Nefrologia, doi:10.3265/Nefrologia.pre2012.Jan.10928 Santos, N. A. G., Catão, C. S., Martins, N. M., Curti, C., Bianchi, M. L. P., & Santos, A. C. (2007). Cisplatin-induced nephrotoxicity is associated with oxidative stress, redox state unbalance, impairment of energetic metabolism and apoptosis in rat kidney mitochondria. Archives of Toxicology, 81(7), 495-504. doi:10.1007/s00204-006-0173-2 Shaki, F., Hosseini, M. J., Ghazi-Khansari, M., & Pourahmad, J. (2012). Toxicity of depleted uranium on isolated rat kidney mitochondria. Biochimica Et Biophysica Acta - General Subjects, 1820(12), 1940-1950. doi:10.1016/j.bbagen.2012.08.015 Soussi, A., Gargouri, M., & El Feki, A. (2018). Effects of co-exposure to lead and zinc on redox status, kidney variables and histopathology in adult albino rats. Toxicology and Industrial Health, 34(7), 469-480. doi:10.1177/0748233718770293 Spreckelmeyer, S., Estrada-Ortiz, N., Prins, G. G. H., van der Zee, M., Gammelgaard, B., Sturup, S., . . . Casini, A. (2017). On the toxicity and transportation mechanisms of cisplatin in kidney tissues in comparison to a gold-based cytotoxic agent. Metallomics, 9, 1786. doi:10.1039/c7mt00271h Turk, E., Kandemir, F. M., Yildirim, S., Caglayan, C., Kucukler, S., & Kuzu, M. (2019). Protective effect of hesperidin on sodium arsenite-induced nephrotoxicity and hepatotoxicity in rats. Biological Trace Element Research, 189, 95-108. doi:10.1007/s12011-018-1443-6 Weber, E. J., Himmelfarb, J., & Kelly, E. J. (2017). Concise review: Current emerging biomarkers of nephrotoxicity. Curr Opin Toxicol., 4, 16-21. doi:10.1016/j.cotox.2017.03.002 Yeh, Y., Lee, Y., Hsieh, Y., & Hwang, D. (2011). Dietary taurine reduces zinc-induced toxicity in male wistar rats. Journal of Food Science, 76(4), 90-98. doi:10.1111/j.1750-3841.2011.02110.x Zamora, L. M., Tracy, B. L., Zielinski, J. M., Meyerhof, D. P., & Moss, M. A. (1998). Chronic ingestion of uranium in drinking water: A study of kidney bioeffects in humans. Toxicological Sciences, 43(1), 68-77. doi:10.1006/toxs.1998.242 AOPWiki 2016-11-29T18:41:27

2022-03-04T10:58:19

Decreased, Glomerular filtration

Tissue

UBERON:0002113

UBERON kidney

Not Specified Not Specified

AOPWiki 2016-11-29T18:41:27

2017-09-16T10:16:29

Decreased, Renal plasma flow

Tissue

UBERON:0002113

UBERON kidney

Moderate Not Specified

AOPWiki 2016-11-29T18:41:27

2017-09-16T10:16:29

Decreased, Sodium reabsorption

Organ

UBERON:0002113

UBERON kidney

Not Specified Not Specified

AOPWiki 2016-11-29T18:41:27

2017-09-16T10:16:29

Increased, Serum creatinine

Organ

UBERON:0001977

UBERON serum

Not Specified Not Specified

AOPWiki 2016-11-29T18:41:27

2017-09-16T10:16:30

Occurrence, Cystic dilatation (renal tubule)

Organ

UBERON:0002113

UBERON kidney

Not Specified Not Specified

AOPWiki 2016-11-29T18:41:27

2017-09-16T10:16:31

Occurrence, Cytoplasmic vacuolization (podocyte)

Organ

UBERON:0002113

UBERON kidney

Not Specified Not Specified

AOPWiki 2016-11-29T18:41:27

2017-09-16T10:16:31

Occurrence, Cytoplasmic vacuolization (Renal tubule)

Organ

UBERON:0002113

UBERON kidney

Not Specified Not Specified

AOPWiki 2016-11-29T18:41:27

2017-09-16T10:16:31

Decreased, Renal ability to dilute urine

Organ

Not Specified Not Specified

AOPWiki 2016-11-29T18:41:27

2016-12-03T16:37:52

Thyroxine (T4) in serum, Decreased

T4 in serum, Decreased

Tissue

All iodothyronines are derived from the modification of tyrosine molecules (Taurog, 2000). There are two biologically active thyroid hormones (THs) in serum, triiodothyronine (T3) and T4, and a few less active iodothyronines, reverse T3 (rT3),  and 3,3'-Diiodothyronine (3,5-T2). T4 is the predominant TH in circulation, comprising approximately 80% of the TH excreted from the thyroid gland in mammals and is the pool from which the majority of T3 in serum is generated (Zoeller et al., 2007). As such, serum T4 changes usually precede changes in other serum THs. Decreased thyroxine (T4) in serum results from one or more MIEs upstream and is considered a key biomarker of altered TH homeostasis (DeVito et al., 1999). Serum T4 is used as a biomarker of TH status because the circulatory system serves as the major transport and delivery system for TH delivery to tissues. The majority of THs in the blood are bound to transport proteins (Bartalena and Robbins, 1993). In serum, it is the unbound, or ‘free’ form of the hormone that is thought to be available for transport into tissues. Free hormones are approximately 0.03 and 0.3 percent for T4 and T3, respectively. There are major species differences in the predominant binding proteins and their affinities for THs (see below). However, there is broad agreement that changes in serum concentrations of THs is diagnostic of thyroid disease or chemical-induced disruption of thyroid homeostasis across vertebrates (DeVito et al., 1999; Miller et al., 2009; Zoeller et al., 2007; Carr and Patiño, 2011). Normal serum T4 reference ranges can be species and lifestage specific. In rodents, serum THs are low in the fetal circulation, increasing as the fetal thyroid gland becomes functional on gestational day 17, just a few days prior to birth. After birth serum hormones increase steadily, peaking at two weeks, and falling slightly to adult levels by postnatal day 21 (Walker et al., 1980; Harris et al., 1978; Goldey et al., 1995; Lau et al., 2003). Similarly, in humans, adult reference ranges for THs do not reflect the normal ranges for children at different developmental stages, with TH concentrations highest in infants, still increased in childhood, prior to a decline to adult levels coincident with pubertal development (Corcoran et al. 1977; Kapelari et al., 2008). In some frog species, there is an analogous peak in THs in tadpoles that starts around embryonic NF stage 56, peaks at stage 62 and the declines to lower levels by stage 56 (Sternberg et al., 2011; Leloup and Buscaglia, 1977).  Additionally, ample evidence is available from studies investigating responses to inhibitors of TH synthesis in fish. For example, Stinckens et al. (2020) showed reduced whole body T4 concentrations in zebrafish larvae exposed to 50 or 100 mg/L methimazole, a potent TPO inhibitor, from immediately after fertilization until 21 or 32 days of age. Exposure to 37 or 111 mg/L propylthiouracil also reduced T4 levels after exposure up to 14, 21 and 32 days in the same study. Walter et al. (2019) showed that propylthiouracil had no effect on T4 levels in 24h old zebrafish, but decreased T4 levels of 72h old zebrafish. This difference is probably due to the onset of embryonic TH production between the age of 24 and 72 hours (Opitz et al., 2011). Stinckens et al. (2016) showed that exposure to 2-mercaptobenzothiazole (MBT), an environmentally relevant TPO inhibitor, decreased whole body T4 levels in continuously exposed 5 and 32 day old zebrafish larvae. A high concentration of MBT also decreased whole body T4 levels in 6 day old fathead minnows, but recovery was observed at the age of 21 days although the fish were kept in the exposure medium (Nelson et al., 2016). Crane et al. (2006) showed decreased T4 levels in 28 day old fathead minnows continuously exposed to 32 or 100 µg/L methimazole.

Serum T3 and T4 can be measured as free (unbound) or total (bound + unbound). Free hormone concentrations are clinically considered more direct indicators of T4 and T3 activities in the body, but in animal studies, total T3 and T4 are typically measured. Historically, the most widely used method in toxicology is the radioimmunoassay (RIA). The method is routinely used in rodent endocrine and toxicity studies. The ELISA method is commonly used as a human clinical test method. Analytical determination of iodothyronines (T3, T4, rT3, T2) and their conjugates, through methods employing HPLC, liquid chromatography, immuno luminescence, and mass spectrometry are less common, but are becoming increasingly available (Hornung et al., 2015; DeVito et al., 1999; Baret and Fert, 1989; Spencer, 2013; Samanidou V.F et al., 2000; Rathmann D. et al., 2015 ). In fish early life stages most evidence for the ontogeny of thyroid hormone synthesis comes from measurements of whole body thyroid hormone levels using LC-MS techniques (Hornung et al., 2015) which are increasingly used to accurately quantify whole body thyroid hormone levels as a proxy for serum thyroid hormone levels (Nelson et al., 2016; Stinckens et al., 2016; Stinckens et al., 2020). It is important to note that thyroid hormones concentrations can be influenced by a number of intrinsic and extrinsic factors (e.g., circadian rhythms, stress, food intake, housing, noise) (see for example, Döhler et al., 1979). Any of these measurements should be evaluated for the relationship to the actual endpoint of interest, repeatability, reproducibility, and lower limits of quantification using a fit-for-purpose approach. This is of particular significance when assessing the very low levels of TH present in fetal serum. Detection limits of the assay must be compatible with the levels in the biological sample. All three of the methods summarized above would be fit-for-purpose, depending on the number of samples to be evaluated and the associated costs of each method. Both RIA and ELISA measure THs by an indirect methodology, whereas analytical determination is the most direct measurement available. All these methods, particularly RIA, are repeatable and reproducible.

Taxonomic: This KE is plausibly applicable across vertebrates and the overall evidence supporting taxonomic applicability is strong. THs are evolutionarily conserved molecules present in all vertebrate species (Hulbert, 2000; Yen, 2001). Moreover, their crucial role in zebrafish development, embryo-to-larval transition and larval-to-juvenile transition (Thienpont et al., 2011; Liu and Chan, 2002), and amphibian and lamprey metamorphoses is well established (Manzon and Youson, 1997; Yaoita and Brown, 1990; Furlow and Neff, 2006). Their role as environmental messenger via exogenous routes in echinoderms confirms the hypothesis that these molecules are widely distributed among the living organisms (Heyland and Hodin, 2004). However, the role of THs in the different species depends on the expression and function of specific proteins (e.g receptors or enzymes) under TH control and may vary across species and tissues. As such, extrapolation regarding TH action across species and developmental stages should be done with caution. With few exceptions, vertebrate species have circulating T4 (and T3) that are bound to transport proteins in blood. Clear species differences exist in serum transport proteins (Dohler et al., 1979; Yamauchi and Isihara, 2009). There are three major transport proteins in mammals; thyroid binding globulin (TBG), transthyretin (TTR), and albumin. In adult humans, the percent bound to these proteins is about 75, 15 and 10 percent, respectively (Schussler 2000).  In contrast, in adult rats the majority of THs are bound to TTR. Thyroid- binding proteins are developmentally regulated in rats. TBG is expressed in rats until approximately postnatal day (PND) 60, with peak expression occurring during weaning (Savu et al., 1989). However, low levels of TBG persist into adult ages in rats and can be experimentally induced by hypothyroidism, malnutrition, or caloric restriction (Rouaze-Romet et al., 1992). While these species differences impact TH half-life (Capen, 1997) and possibly regulatory feedback mechanisms, there is little information on quantitative dose-response relationships of binding proteins and serum hormones during development across different species. Serum THs are still regarded as the most robust measurable key event causally linked to downstream adverse outcomes. Life stage: The earliest life stages of teleost fish rely on maternally transferred THs to regulate certain developmental processes until embryonic TH synthesis is active (Power et al., 2001). As a result, T4 levels are not expected to decrease in response to exposure to inhibitors of TH synthesis during these earliest stages of development. In zebrafish, Opitz et al. (2011) showed the formation of a first thyroid follicle at 55 hours post fertilization (hpf), Chang et al. (2012) showed a first significant TH increase at 120 hpf and Walter et al. (2019) showed clear TH production already at 72 hpf but did not analyse time points between 24 and 72 hpf. In fathead minnows, a significant increase of whole body TH levels was already observed between 1 and 2 dpf, which corresponds to the appearance of the thyroid anlage at 35 hpf prior to the first observation of thyroid follicles at 58 hpf (Wabuke-Bunoti and Firling, 1983). It is still uncertain when exactly embryonic TH synthesis is activated and how this determines sensitivity to TH system disruptors. Sex: The KE is plausibly applicable to both sexes. THs are essential in both sexes and the components of the HPT-axis are identical in both sexes. There can however be sex-dependent differences in the sensitivity to the disruption of TH levels and the magnitude of the response. In humans, females appear more susceptible to hypothyroidism compared to males when exposed to certain halogenated chemicals (Hernandez‐Mariano et al., 2017; Webster et al., 2014). In adult zebrafish, Liu et al. (2019) showed sex-dependent changes in TH levels and mRNA expression of regulatory genes including corticotropin releasing hormone (crh), thyroid stimulating hormone (tsh) and deiodinase 2 after exposure to organophosphate flame retardants. The underlying mechanism of any sex-related differences remains unclear.

UBERON:0001977

UBERON serum

High Female High Male

High

All life stages

High High High Moderate Moderate High High High

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General and Comparative Endocrinology. 170(2):299-312. Chang J, Wang M, Gui W, Zhao Y, Yu L, Zhu G. 2012. Changes in thyroid hormone levels during zebrafish development. Zoological Science. 29(3):181-184. Cope RB, Kacew S, Dourson M. A reproductive, developmental and neurobehavioral study following oral exposure of tetrabromobisphenol A on Sprague-Dawley rats. Toxicology. 2015 329:49-59. Corcoran JM, Eastman CJ, Carter JN, Lazarus L. (1977). Circulating thyroid hormone levels in children. Arch Dis Child. 52: 716-720. Crane HM, Pickford DB, Hutchinson TH, Brown JA. 2006. The effects of methimazole on development of the fathead minnow, pimephales promelas, from embryo to adult. Toxicological Sciences. 93(2):278-285. Crofton KM. Developmental disruption of thyroid hormone: correlations with hearing dysfunction in rats. Risk Anal. 2004 Dec;24(6):1665-71. DeVito M, Biegel L, Brouwer A, Brown S, Brucker-Davis F, Cheek AO, Christensen R, Colborn T, Cooke P, Crissman J, Crofton K, Doerge D, Gray E, Hauser P, Hurley P, Kohn M, Lazar J, McMaster S, McClain M, McConnell E, Meier C, Miller R, Tietge J, Tyl R. (1999). Screening methods for thyroid hormone disruptors. Environ Health Perspect. 107:407-415. Döhler KD, Wong CC, von zur Mühlen A (1979).   The rat as model for the study of drug effects on thyroid function: consideration of methodological problems.  Pharmacol Ther B. 5:305-18. Eales JG. (1997). Iodine metabolism and thyroid related functions in organisms lacking thyroid follicles: Are thyroid hormones also vitaminsProc Soc Exp Biol Med. 214:302-317. Furlow JD, Neff ES. (2006). A developmental switch induced by thyroid hormone: Xenopus laevis metamorphosis. Trends Endocrinol Metab. 17:40–47. Goldey ES, Crofton KM. Thyroxine replacement attenuates hypothyroxinemia, hearing loss, and motor deficits following developmental exposure to Aroclor 1254 in rats. Toxicol Sci. 1998 45(1):94-10 Goldey ES, Kehn LS, Lau C, Rehnberg GL, Crofton KM.  Developmental exposure to polychlorinated biphenyls (Aroclor 1254) reduces circulating thyroid hormone concentrations and causes hearing deficits in rats. Tox Appl Pharmacol. 1995 135(1):77-88. Harris AR, Fang SL, Prosky J, Braverman LE, Vagenakis AG.  Decreased outer ring monodeiodination of thyroxine and reverse triiodothyronine in the fetal and neonatal rat.  Endocrinology. 1978 Dec;103(6):2216-22 Hernandez-Mariano JA, Torres-Sanchez L, Bassol-Mayagoitia S, Escamilla-Nunez M, Cebrian ME, Villeda-Gutierrez EA, Lopez-Rodriguez G, Felix-Arellano EE, Blanco-Munoz J. 2017. Effect of exposure to p,p '-dde during the first half of pregnancy in the maternal thyroid profile of female residents in a mexican floriculture area. Environmental Research. 156:597-604. Heyland A, Hodin J. (2004). Heterochronic developmental shift caused by thyroid hormone in larval sand dollars and its implications for phenotypic plasticity and the evolution of non-feeding development. Evolution. 58: 524-538. Heyland A, Moroz LL. (2005). Cross-kingdom hormonal signaling: an insight from thyroid hormone functions in marine larvae. J Exp Biol. 208:4355-4361. Hill RN, Crisp TM, Hurley PM, Rosenthal SL, Singh DV. Risk assessment of thyroid follicular cell tumors.  Environ Health Perspect. 1998 Aug;106(8):447-57. Hornung MW, Kosian P, Haselman J, Korte J, Challis K, Macherla C, Nevalainen E, Degitz S (2015) In vitro, ex vivo and in vivo determination of thyroid hormone modulating activity of benzothiazoles. Toxicol Sci 146:254-264. Hulbert AJ. Thyroid hormones and their effects: a new perspective. Biol Rev Camb Philos Soc. 2000 Nov;75(4):519-631. Review. Kapelari K, Kirchlechner C, Högler W, Schweitzer K, Virgolini I, Moncayo R. 2008. Pediatric reference intervals for thyroid hormone levels from birth to adulthood: a retrospective study. BMC Endocr Disord. 8: 15. Lau C, Thibodeaux JR, Hanson RG, Rogers JM, Grey BE, Stanton ME, Butenhoff JL, Stevenson LA.  Exposure to perfluorooctane sulfonate during pregnancy in rat and mouse. II: postnatal evaluation.  Toxicol Sci. 2003 Aug;74(2):382-92. Leloup, J., and M. Buscaglia. La triiodothyronine: hormone de la métamorphose des amphibiens. CR Acad Sci 284 (1977): 2261-2263. Liu J, Liu Y, Barter RA, Klaassen CD.: Alteration of thyroid homeostasis by UDP-glucuronosyltransferase inducers in rats: a dose-response study. J Pharmacol Exp Ther 273, 977-85, 1994 Liu XS, Cai Y, Wang Y, Xu SH, Ji K, Choi K. 2019. Effects of tris(1,3-dichloro-2-propyl) phosphate (tdcpp) and triphenyl phosphate (tpp) on sex-dependent alterations of thyroid hormones in adult zebrafish. Ecotoxicology and Environmental Safety. 170:25-32. Liu YW, Chan WK. 2002. Thyroid hormones are important for embryonic to larval transitory phase in zebrafish. Differentiation. 70(1):36-45. Manzon RG, Youson JH. (1997). The effects of exogenous thyroxine (T4) or triiodothyronine (T3), in the presence and absence of potassium perchlorate, on the incidence of metamorphosis and on serum T4 and T3 concentrations in larval sea lampreys (Petromyzon marinus L.). Gen Comp Endocrinol. 106:211-220.  McClain RM. Mechanistic considerations for the relevance of animal data on thyroid neoplasia to human risk assessment. Mutat Res. 1995 Dec;333(1-2):131-42 Miller MD, Crofton KM, Rice DC, Zoeller RT.  Thyroid-disrupting chemicals: interpreting upstream biomarkers of adverse outcomes. Environ Health Perspect. 2009 117(7):1033-41 Morse DC, Wehler EK, Wesseling W, Koeman JH, Brouwer A. Alterations in rat brain thyroid hormone status following pre- and postnatal exposure to polychlorinated biphenyls (Aroclor 1254). Toxicol Appl Pharmacol. 1996 Feb;136(2):269-79. Nelson K, Schroeder A, Ankley G, Blackwell B, Blanksma C, Degitz S, Flynn K, Jensen K, Johnson R, Kahl M et al. 2016. Impaired anterior swim bladder inflation following exposure to the thyroid peroxidase inhibitor 2-mercaptobenzothiazole part i: Fathead minnow. Aquatic Toxicology. 173:192-203. NTP National Toxicology Program.: NTP toxicology and carcinogenesis studies of 3,3'-dimethylbenzidine dihydrochloride (CAS no. 612-82-8) in F344/N rats (drinking water studies). Natl Toxicol Program Tech Rep Ser 390, 1-238, 1991. O'Connor, J. C., J. C. Cook, et al. (1998). "An ongoing validation of a Tier I screening battery for detecting endocrine-active compounds (EACs)." Toxicol Sci 46(1): 45-60. O'Connor, J. C., L. G. Davis, et al. (2000). "Detection of dopaminergic modulators in a tier I screening battery for identifying endocrine-active compounds (EACs)." Reprod Toxicol 14(3): 193-205. Opitz R, Maquet E, Zoenen M, Dadhich R, Costagliola S. 2011. Tsh receptor function is required for normal thyroid differentiation in zebrafish. Molecular Endocrinology. 25(9):1579-1599. Power DM, Llewellyn L, Faustino M, Nowell MA, Bjornsson BT, Einarsdottir IE, Canario AV, Sweeney GE. 2001. Thyroid hormones in growth and development of fish. Comp Biochem Physiol C Toxicol Pharmacol. 130(4):447-459. Rathmann D, Rijntjes E, Lietzow J, Köhrle J. (2015) Quantitative Analysis of Thyroid Hormone Metabolites in Cell Culture Samples Using LC-MS/MS. Eur Thyroid J. Sep;4(Suppl 1):51-8. Rouaze-Romet M, Savu L, Vranckx R, Bleiberg-Daniel F, Le Moullac B, Gouache P, Nunez EA. 1992. Reexpression of thyroxine-binding globulin in postweaning rats during protein or energy malnutrition. Acta Endocrinol (Copenh).127:441-448. Samanidou VF, Kourti PV. (2009) Rapid HPLC method for the simultaneous monitoring of duloxetine, venlaflaxine, fluoxetine and paroxetine in biofluids. Bioanalysis. 2009 Aug;1(5):905-17. Savu L, Vranckx R, Maya M, Gripois D, Blouquit MF, Nunez EA. 1989. Thyroxine-binding globulin and thyroxinebinding prealbumin in hypothyroid and hyperthyroid developing rats. BiochimBiophys Acta. 992:379-384. Schneider S, Kaufmann W, Strauss V, van Ravenzwaay B.    Vinclozolin: a feasibility and sensitivity study of the ILSI-HESI F1-extended one-generation rat reproduction protocol. Regul Toxicol Pharmacol. 2011 Feb;59(1):91-100. Schussler, G.C. (2000). The thyroxine-binding proteins. Thyroid 10:141–149. Spencer, CA. (2013). Assay of thyroid hormone and related substances. In De Groot, LJ et al. (Eds). Endotext. South Dartmouth, MA Sternberg RM, Thoemke KR, Korte JJ, Moen SM, Olson JM, Korte L, Tietge JE, Degitz SJ Jr. Control of pituitary thyroid-stimulating hormone synthesis and secretion by thyroid hormones during Xenopus metamorphosis. Gen Comp Endocrinol. 2011. 173(3):428-37 Stinckens E, Vergauwen L, Blackwell BR, Anldey GT, Villeneuve DL, Knapen D. 2020. Effect of thyroperoxidase and deiodinase inhibition on anterior swim bladder inflation in the zebrafish. Environmental Science & Technology. 54(10):6213-6223. Stinckens E, Vergauwen L, Schroeder A, Maho W, Blackwell B, Witters H, Blust R, Ankley G, Covaci A, Villeneuve D et al. 2016. Impaired anterior swim bladder inflation following exposure to the thyroid peroxidase inhibitor 2-mercaptobenzothiazole part ii: Zebrafish. Aquatic Toxicology. 173:204-217. Taurog A. 2005. Hormone synthesis. In: Werner and Ingbar’s The Thyroid: A Fundamental and Clinical Text (Braverman LE, Utiger RD, eds). Philadelphia:Lippincott, Williams and Wilkins, 47–81Walker P, Dubois JD, Dussault JH.  Free thyroid hormone concentrations during postnatal development in the rat.  Pediatr Res. 1980 Mar;14(3):247-9. Thienpont B, Tingaud-Sequeira A, Prats E, Barata C, Babin PJ, Raldúa D. Zebrafish eleutheroembryos provide a suitable vertebrate model for screening chemicals that impair thyroid hormone synthesis. Environ Sci Technol. 2011 Sep 1;45(17):7525-32. Wabukebunoti MAN, Firling CE. 1983. The prehatching development of the thyroid-gland of the fathead minnow, pimephales-promelas (rafinesque). General and Comparative Endocrinology. 49(2):320-331. Walter KM, Miller GW, Chen XP, Yaghoobi B, Puschner B, Lein PJ. 2019. Effects of thyroid hormone disruption on the ontogenetic expression of thyroid hormone signaling genes in developing zebrafish (danio rerio). General and Comparative Endocrinology. 272:20-32. Webster GM, Venners SA, Mattman A, Martin JW. 2014. Associations between perfluoroalkyl acids (pfass) and maternal thyroid hormones in early pregnancy: A population-based cohort study. Environmental Research. 133:338-347. Yamauchi K1, Ishihara A. Evolutionary changes to transthyretin: developmentally regulated and tissue-specific gene expression. FEBS J. 2009. 276(19):5357-66. Yaoita Y, Brown DD. (1990). A correlation of thyroid hormone receptor gene expression with amphibian metamorphosis. Genes Dev. 4:1917-1924. Yen PM. (2001). Physiological and molecular basis of thyroid hormone action. Physiol Rev. 81:1097-1142. Zoeller RT, Tan SW, Tyl RW. General background on the hypothalamic-pituitary-thyroid (HPT) axis. Crit Rev Toxicol. 2007 Jan-Feb;37(1-2):11-53 Zoeller, R. T., R. Bansal, et al. (2005). "Bisphenol-A, an environmental contaminant that acts as a thyroid hormone receptor antagonist in vitro, increases serum thyroxine, and alters RC3/neurogranin expression in the developing rat brain." Endocrinology 146(2): 607-612. AOPWiki 2016-11-29T18:41:23

2022-10-10T08:52:30

<upstream-id>784e397f-8917-429e-8122-f34d2ce9495f</upstream-id> <downstream-id>ba8016f1-3f6a-465d-a73e-9d9fb4da63f6</downstream-id> Thyroid hormones (THs), thyroxine (T4) and triiodothyronine (T3) are synthesized by NIS and TPO in the thyroid gland as iodinated thyroglobulin (Tg) and stored in the colloid of thyroid follicles across vertebrates. Secretion from the follicle into serum is a multi-step process. The first involves thyroid stimulating hormone (TSH) stimulation of the separation of the peptide linkage between Tg and TH. The next steps involve endocytosis of colloid, fusion of the endosome with the basolateral membrane of the thyrocyte, and finally release of TH into blood. More detailed descriptions of this process can be found in reviews by Braverman and Utiger (2012) and Zoeller et al. (2007).

The weight of evidence linking these two KEs of decreased TH synthesis and decreased T4 in serum is strong. It is commonly accepted dogma that decreased synthesis in the thyroid gland will result in decreased circulating TH (serum T4).

The biological relationship between two KEs in this KER is well understood and documented fact within the scientific community.

It is widely accepted that TPO inhibition leads to declines in serum T4 levels in adult mammals. This is due to the fact that the sole source for circulating T4 derives from hormone synthesis in the thyroid gland. Indeed, it has been known for decades that insufficient dietary iodine will lead to decreased serum TH concentrations due to inadequate synthesis. Strong qualitative and quantitative relationships exist between reduced TH synthesis and reduced serum T4 (Ekerot et al., 2013; Degon et al., 2008; Cooper et al., 1982; 1983; Leonard et al., 2016; Zoeller and Tan, 2007).  There is more limited evidence supporting the relationship between decreased TH synthesis and lowered circulating hormone levels during development.  Lu and Anderson (1994) followed the time course of TH synthesis, measured as thyroxine secretion rate, in non-treated pregnant rats and correlated it with serum T4 levels. Modeling of TH in the rat fetus demonstrates the quantitative relationship between TH synthesis and serum T4 concentrations (Hassan et al., 2017, 2020; Handa et al., 2021). Furthermore, a wide variety of drugs and chemicals that inhibit TPO are known to result in decreased release of TH from the thyroid gland, as well as decreased circulating TH concentrations. This is evidenced by a very large number of studies that employed a wide variety of techniques, including thyroid gland explant cultures, tracing organification of 131-I and in vivo treatment of a variety of animal species with known TPO inhibitors (King and May,1984; Atterwill et al., 1990; Brown et al., 1986; Brucker-Davis, 1998; Haselman et al., 2020; Hornung et al., 2010; Hurley et al., 1998; Kohrle, 2008; Tietge et al., 2010). Additionally, evidence is available from studies investigating responses to TPO inhibitors in fish. For example, Stinckens et al. (2020) showed reduced whole body T4 concentrations in zebrafish larvae exposed to 50 or 100 mg/L methimazole, a potent TPO inhibitor, from immediately after fertilization until 21 or 32 days of age. Exposure to 37 or 111 mg/L propylthiouracil also reduced T4 levels after exposure up to 14, 21 and 32 days in the same study. Walter et al. (2019) showed that propylthiouracil had no effect on T4 levels in 24h old zebrafish, but decreased T4 levels of 72h old zebrafish. This difference is probably due to the onset of embryonic TH production between the age of 24 and 72 hours (Opitz et al., 2011). Stinckens et al. (2016) showed that exposure to 2-mercaptobenzothiazole (MBT), an environmentally relevant TPO inhibitor, decreased whole body T4 levels in continuously exposed 5 and 32 day old zebrafish larvae. Several other studies have also shown that chemically induced Inhibition of TPO results in reduced TH synthesis in zebrafish (Van der Ven et al., 2006; Raldua and Babin, 2009; Liu et al., 2011; Thienpont et al., 2011; Rehberger et al., 2018). A high concentration of MBT also decreased whole body T4 levels in 6 day old fathead minnows, but recovery was observed at the age of 21 days although the fish were kept in the exposure medium (Nelson et al., 2016). Crane et al. (2006) showed decreased T4 levels in 28 day old fathead minnows continuously exposed to 32 or 100 µg/L methimazole. Temporal Evidence: In mammals, the temporal nature of this KER is applicable to all life stages, including development (Seed et al., 2005).  There are currently no studies that measured both TPO synthesis and TH production during development. However, the impact of decreased TH synthesis on serum hormones is similar across all ages in mammals. Good evidence for the temporal relationship comes from thyroid system modeling of the impacts of iodine deficiency and NIS inhibition (e.g., Degon et al., 2008; Fisher et al., 2013). In addition, recovery experiments have demonstrated that serum thyroid hormones recovered in athyroid mice following grafting of in-vitro derived follicles (Antonica et al., 2012). In Xenopus, it has been shown that depression of TH synthesis in the thyroid gland precedes depression of circulating TH within 7 days of exposure during pro-metamorphosis (Haselman et al., 2020).    In oviparous fish such as zebrafish and fathead minnow, the nature of this KER depends on the life stage since the earliest stages of embryonic development rely on maternal THs transferred to the eggs. Embryonic TH synthesis is activated later during embryo-larval development. (See Domain of applicability) Dose-response Evidence: Dose-response data is lacking from studies that include concurrent measures of both TH synthesis and serum TH concentrations. However, data is available demonstrating correlations between thyroidal TH and serum TH concentrations during gestation and lactation during development (Gilbert et al., 2013). This data was used to develop a rat quantitative biologically-based dose-response model for iodine deficiency (Fisher et al., 2013). In Xenopus, dose-responses were demonstrated in both thyroidal T4 and circulating T4 following exposure to three TPO inhibitors (Haselman et al., 2020).

There are no inconsistencies in this KER, but there are some uncertainties. The first uncertainty stems from the paucity of data for quantitative modeling of the relationship between the degree of synthesis decrease and resulting changes in circulating T4 concentrations. In addition, most of the data supporting this KER comes from inhibition of TPO, and there are a number of other processes (e.g., endocytosis, lysosomal fusion, basolateral fusion and release) that are not as well studied. For example, Kim et al. (2015) investigated the adverse effects of Triphenyl phosphate (TPP), a substance that disrupts the thyroid system. Therefore, Rat pituitary (GH3) and thyroid follicular cell lines (FRTL-5) were studied. In the GH3 cells, TPP led to an upregulation of the expression of important thyroid genes (tsh, tr alpha and tr beta) while T3, a positive control, downregulated the expression of these genes. In FRTL-5 cells, the expression of nis and tpo genes was significantly upregulated, suggesting that TPP stimulates TH synthesis in the thyroid gland. In zebrafish larvae at the age of 7 days post-fertilisation (dpf), TPP exposure resulted in a significant increase in T3 and T4 concentrations and the expression of genes involved in thyroid hormone synthesis. Exposure to TPP also significantly regulated the expression of genes involved in the metabolism (dio1), transport (ttr) and excretion (ugt1ab) of THs. The down-regulation of the crh and tsh genes in the zebrafish larvae suggests the activation of a central regulatory feedback mechanism that is triggered by the increased T3 levels in vivo. Taken together, these observations indicate that TPP increases TH concentrations in early life stages of zebrafish by disrupting central regulatory and hormone synthesis pathways.

During Xenopus metamorphosis, circulating T4 steadily increases to peak levels at metamorphic climax. Therefore, during Xenopus metamorphosis, this KER is operable at an increased rate as compared to a system that is maintaining steady circulating T4 levels through homeostatic control. In this case, developmental status is a modulating factor for the rates and trajectories of these KEs.

In rats, Hassan et al. (2020) demonstrated in vitro: ex vivo correlations of TPO inhibition using PTU and MMI and constructed a quantitative model relating level of TPO inhibition with changes in circulating T4 levels. They determined that 30% inhibition of TPO was sufficient to decrease circulating T4 levels by 20%. This is further supported by studies of Hassan et al. (2017) and Handa et al. (2021) In Xenopus, Haselman et al. (2020) collected temporal and dose-response data for both thyroidal and circulating T4 which showed strong qualitative concordance of the response-response relationship. A quantitative relationship exists there in, but is yet to be demonstrated mathematically in this species.

Fisher et al. (2013) published a quantitative biologically-based dose-response model for iodine deficiency in the rat. This model provides quantitative relationships for thyroidal T4 synthesis (iodine organification) and predictions of serum T4 concentrations in developing rats. There are other computational models that include thyroid hormone synthesis. Ekerot et al. (2012) modeled TPO, T3, T4 and TSH in dogs and humans based on exposure to myeloperoxidase inhibitors that also inhibit TPO.  This model was recently adapted for rats(Leonard et al., 2016) and Hassan et al (2017) have extended it to include the pregnant rat dam in response to TPO inhibition induced by PTU. While the original model predicted serum TH and TSH levels as a function of oral dose, it was not used to explicitly predict the relationship between serum hormones and TPO inhibition, or TH synthesis. Leonard et al. (2016) recently incorporated TPO inhibition into the model. Degon et al (2008) developed a human thyroid model that includes TPO, but does not make quantitative prediction of organification changes due to inhibition of the TPO enzyme. Further empirical support for the response-response relationship has been demonstrated in the amphibian model, Xenopus laevis, exposed to TPO inhibitors during pro-metamorphosis (Haselman et al., 2020) wherein temporal profiles were measured for both thyroidal and circulating T4.

Given that the thyroid gland contains follicular lumen space filled with stored thyroglobulin/T4, complete inhibition of thyroid hormone synthesis at a given point in time will not result in an instantaneous decrease in circulating T4. The system will be capable of maintaining sufficient circulating T4 levels until the gland stores are depleted. The time it takes to deplete stored hormone will greatly depend on species, developmental status and numerous other factors. In Xenopus, Haselman et al. (2020) demonstrated an approximately 5 day difference between a significant decrease in thyroidal T4 preceding a significant decrease in circulating T4 while exposed to a potent TPO inhibitor (MMI) continuously during pro-metamorphosis.

This KER is entirely influenced by the feedback loop between circulating T4 originating from the thyroid gland and circulating TSH originating from the pituitary. Intermediate biochemical processes exist within the hypothalamus to affirm feedback and coordinately release TSH from the pituitary. However, quantitative representations of these feedback processes are limited to models discussed previously. In Xenopus, circulating levels of T4 increase through pro-metamorphosis indicating a "release" of feedback to allow circulating levels of T4 to increase and drive metamorphic changes (Sternberg et al., 2011). This provides evidence that homeostatic control of feedback can be developmentally dependent, and likely species dependent.

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Alexander EK, Pearce EN, Brent GA, Brown RS, Chen H, Dosiou C, Grobman WA, Laurberg P, Lazarus JH, Mandel SJ, Peeters RP, Sullivan S.  2017 Guidelines of the American Thyroid Association for the Diagnosis and Management of Thyroid Disease During Pregnancy and the Postpartum. Thyroid. 2017 Mar;27(3):315-389. Antonica F, Kasprzyk DF, Opitz R, Iacovino M, Liao XH, Dumitrescu AM, Refetoff S, Peremans K, Manto M, Kyba M, Costagliola S.  Generation of functional thyroid from embryonic stem cells.  Nature. 2012 491(7422):66-71. Atterwill CK, Fowler KF. A comparison of cultured rat FRTL-5 and porcine thyroid cells for predicting the thyroid toxicity of xenobiotics. Toxicol In Vitro. 1990. 4(4-5):369-74. Braverman, L.E. and Utiger, R.D. (2012). Werner and Ingbar's The Thyroid: A Fundamental and Clinical Text (10 ed.). Philadelphia, PA: Lippincott Williams & Wilkins. pp. 775-786. ISBN 978-1451120639. Brown CG, Fowler KL, Nicholls PJ, Atterwill C. Assessment of thyrotoxicity using in vitro cell culture systems. Food Chem Toxicol. 1986 24(6-7):557-62. Brucker-Davis F. Effects of environmental synthetic chemicals on thyroid function. Thyroid. 1998 8(9):827-56. Chang J, Wang M, Gui W, Zhao Y, Yu L, Zhu G. 2012. Changes in thyroid hormone levels during zebrafish development. Zoological Science. 29(3):181-184. Cooper DS, Kieffer JD, Halpern R, Saxe V, Mover H, Maloof F, Ridgway EC (1983) Propylthiouracil (PTU) pharmacology in the rat. II. Effects of PTU on thyroid function. Endocrinology 113:921-928. Cooper DS, Saxe VC, Meskell M, Maloof F, Ridgway EC.Acute effects of propylthiouracil (PTU) on thyroidal iodide organification and peripheral iodothyronine deiodination: correlation with serum PTU levels measured by radioimmunoassay. J Clin Endocrinol Metab. 1982 54(1):101-7. Crane HM, Pickford DB, Hutchinson TH, Brown JA. 2006. The effects of methimazole on development of the fathead minnow, pimephales promelas, from embryo to adult. Toxicological Sciences. 93(2):278-285. Degon, M., Chipkin, S.R., Hollot, C.V., Zoeller, R.T., and Chait, Y. (2008). A computational model of the human thyroid. Mathematical Biosciences 212, 22–53 Ekerot P, Ferguson D, Glämsta EL, Nilsson LB, Andersson H, Rosqvist S, Visser SA. Systems pharmacology modeling of drug-induced modulation of thyroid hormones in dogs and translation to human. Pharm Res. 2013 30(6):1513-24. Fisher JW, Li S, Crofton K, Zoeller RT, McLanahan ED, Lumen A, Gilbert ME.  Evaluation of iodide deficiency in the lactating rat and pup using a biologically based dose-response model. Toxicol Sci. 2013 132(1):75-86. Gilbert ME, Hedge JM, Valentín-Blasini L, Blount BC, Kannan K, Tietge J, Zoeller RT, Crofton KM, Jarrett JM, Fisher JW.  An animal model of marginal iodine deficiency during development: the thyroid axis and neurodevelopmental outcome.  Toxicol Sci. 2013 132(1):177-95. Handa S, Hassan I, Gilbert M, El-Masri H. 2021. Mechanistic Computational Model for Extrapolating In Vitro Thyroid Peroxidase (TPO) Inhibition Data to Predict Serum Thyroid Hormone Levels in Rats. Toxicological Sciences 183(1):36-48. Haselman, J.T., Olker, J.H., Kosian, P.A., Korte, J.J., Swintek, J.A., Denny, J.S., Nichols, J.W., Tietge, J.E., Hornung, M.W. and Degitz, S.J., 2020. Targeted pathway-based in vivo testing using thyroperoxidase inhibition to evaluate plasma thyroxine as a surrogate metric of metamorphic success in model amphibian Xenopus laevis. Toxicological Sciences, 175(2), pp.236-250. Hassan, I, El-Masri, H., Kosian, PA, Ford, J, Degitz, SJ and Gilbert, ME. Quantitative Adverse Outcome Pathway for Neurodevelopmental Effects of Thyroid Peroxidase-Induced Thyroid Hormone Synthesis Inhibition. Toxicol Sci. 2017 Nov 1;160(1):57-73 Hassan, I., El-Masri, H., Ford, J., Brennan, A., Handa, S., Paul Friedman, K. and Gilbert, M.E., 2020. Extrapolating in vitro screening assay data for thyroperoxidase inhibition to predict serum thyroid hormones in the rat. Toxicological Sciences, 173(2), pp.280-292. Hernandez-Mariano JA, Torres-Sanchez L, Bassol-Mayagoitia S, Escamilla-Nunez M, Cebrian ME, Villeda-Gutierrez EA, Lopez-Rodriguez G, Felix-Arellano EE, Blanco-Munoz J. 2017. Effect of exposure to p,p '-dde during the first half of pregnancy in the maternal thyroid profile of female residents in a mexican floriculture area. Environmental Research. 156:597-604. Hornung MW, Degitz SJ, Korte LM, Olson JM, Kosian PA, Linnum AL, Tietge JE. Inhibition of thyroid hormone release from cultured amphibian thyroid glands by methimazole, 6-propylthiouracil, and perchlorate. Toxicol Sci. 2010 118(1):42-51. Hurley PM. Mode of carcinogenic action of pesticides inducing thyroid follicular cell tumors in rodents. Environ Health Perspect. 1998 106(8):437-45. Kim, S., Jung, J., Lee, I., Jung, D., Youn, H., & Choi, K. (2015). Thyroid disruption by triphenyl phosphate, an organophosphate flame retardant, in zebrafish (Danio rerio) embryos/larvae, and in GH3 and FRTL-5 cell lines. Aquatic Toxicology, 160, 188–196. https://doi.org/10.1016/j.aquatox.2015.01.016 King DB, May JD. Thyroidal influence on body growth. J Exp Zool. 1984 Dec;232(3):453-60. Köhrle J. Environment and endocrinology: the case of thyroidology. Ann Endocrinol (Paris). 2008 69(2):116-22. Leonard JA, Tan YM, Gilbert M, Isaacs K, El-Masri H. Estimating margin of exposure to thyroid peroxidase inhibitors using high-throughput in vitro data, high-throughput exposure modeling, and physiologically based pharmacokinetic/pharmacodynamic modeling. Toxicol Sci. 2016 151(1):57-70. Liu CS, Zhang XW, Deng J, Hecker M, Al-Khedhairy A, Giesy JP, Zhou BS. 2011. Effects of prochloraz or propylthiouracil on the cross-talk between the hpg, hpa, and hpt axes in zebrafish. Environmental Science & Technology. 45(2):769-775. Liu XS, Cai Y, Wang Y, Xu SH, Ji K, Choi K. 2019. Effects of tris(1,3-dichloro-2-propyl) phosphate (tdcpp) and triphenyl phosphate (tpp) on sex-dependent alterations of thyroid hormones in adult zebrafish. Ecotoxicology and Environmental Safety. 170:25-32. Lu, M-H, and Anderson, RR. Thyroxine secretion rats during pregnancy in the rat.  Endo Res. 1994. 20(4):343-364. Nelson K, Schroeder A, Ankley G, Blackwell B, Blanksma C, Degitz S, Flynn K, Jensen K, Johnson R, Kahl M et al. 2016. Impaired anterior swim bladder inflation following exposure to the thyroid peroxidase inhibitor 2-mercaptobenzothiazole part i: Fathead minnow. Aquatic Toxicology. 173:192-203. Opitz R, Maquet E, Zoenen M, Dadhich R, Costagliola S. 2011. Tsh receptor function is required for normal thyroid differentiation in zebrafish. Molecular Endocrinology. 25(9):1579-1599. Paul KB, Hedge JM, Macherla C, Filer DL, Burgess E, Simmons SO, Crofton KM, Hornung MW. Cross-species analysis of thyroperoxidase inhibition by xenobiotics demonstrates conservation of response between pig and rat. Toxicology. 2013. 312:97-107. Power DM, Llewellyn L, Faustino M, Nowell MA, Bjornsson BT, Einarsdottir IE, Canario AV, Sweeney GE. 2001. Thyroid hormones in growth and development of fish. Comp Biochem Physiol C Toxicol Pharmacol. 130(4):447-459. Raldua D, Babin PJ. 2009. Simple, rapid zebrafish larva bioassay for assessing the potential of chemical pollutants and drugs to disrupt thyroid gland function. Environmental Science & Technology. 43(17):6844-6850. Rehberger K, Baumann L, Hecker M, Braunbeck T. 2018. Intrafollicular thyroid hormone staining in whole-mount zebrafish (danio rerio) embryos for the detection of thyroid hormone synthesis disruption. Fish Physiology and Biochemistry. 44(3):997-1010. Sternberg, R.M., Thoemke, K.R., Korte, J.J., Moen, S.M., Olson, J.M., Korte, L., Tietge, J.E. and Degitz Jr, S.J., 2011. Control of pituitary thyroid-stimulating hormone synthesis and secretion by thyroid hormones during Xenopus metamorphosis. General and comparative endocrinology, 173(3), pp.428-437. Stinckens E, Vergauwen L, Blackwell BR, Anldey GT, Villeneuve DL, Knapen D. 2020. Effect of thyroperoxidase and deiodinase inhibition on anterior swim bladder inflation in the zebrafish. Environmental Science & Technology. 54(10):6213-6223. Stinckens E, Vergauwen L, Schroeder A, Maho W, Blackwell B, Witters H, Blust R, Ankley G, Covaci A, Villeneuve D et al. 2016. Impaired anterior swim bladder inflation following exposure to the thyroid peroxidase inhibitor 2-mercaptobenzothiazole part ii: Zebrafish. Aquatic Toxicology. 173:204-217. Thienpont B, Tingaud-Sequeira A, Prats E, Barata C, Babin PJ, Raldua D. 2011. Zebrafish eleutheroembryos provide a suitable vertebrate model for screening chemicals that impair thyroid hormone synthesis. Environmental Science & Technology. 45(17):7525-7532. Tietge, J.E., Butterworth, B.C., Haselman, J.T., Holcombe, G.W., Hornung, M.W., Korte, J.J., Kosian, P.A., Wolfe, M. and Degitz, S.J., 2010. Early temporal effects of three thyroid hormone synthesis inhibitors in Xenopus laevis. Aquatic Toxicology, 98(1), pp.44-50. van der Ven LTM, van den Brandhof EJ, Vos JH, Power DM, Wester PW. 2006. Effects of the antithyroid agent propylthiouracil in a partial life cycle assay with zebrafish. Environmental Science & Technology. 40(1):74-81. Van Herck SL, Geysens S, Delbaere J, Darras VM.  Regulators of thyroid hormone availability and action in embryonic chicken brain development. Gen Comp Endocrinol. 2013. 190:96-104. Wabukebunoti MAN, Firling CE. 1983. The prehatching development of the thyroid-gland of the fathead minnow, pimephales-promelas (rafinesque). General and Comparative Endocrinology. 49(2):320-331. Walter KM, Miller GW, Chen XP, Yaghoobi B, Puschner B, Lein PJ. 2019. Effects of thyroid hormone disruption on the ontogenetic expression of thyroid hormone signaling genes in developing zebrafish (danio rerio). General and Comparative Endocrinology. 272:20-32. Webster GM, Venners SA, Mattman A, Martin JW. 2014. Associations between perfluoroalkyl acids (pfass) and maternal thyroid hormones in early pregnancy: A population-based cohort study. Environmental Research. 133:338-347. Zoeller, R. T., Tan, S. W., and Tyl, R. W. (2007). General background on the hypothalamic-pituitary-thyroid (HPT) axis. Critical reviews in toxicology 37(1-2), 11-53. AOPWiki 2016-11-29T18:41:33

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Kidney dysfunction by decreased thyroid hormone

Kidney dysfunction

Jung-Hwa Oh

BY-SA

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